Variation in the Cave Environment and its Biological Implications

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Bat Conservation and Management Workshop Course Booklet Portal, Arizona 2011 Field Site: American Museum of Natural History Southwestern Research Station Led by: Janet Tyburec Bat Conservation International John Chenger Bat Conservatio n and Management Tim Snow Arizona Game and Fish Department Cullen Geiselman, PhD BCI Board Member ©Bat Conservation International May 2011


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Special Thanks The production of these workshops would not be possible without the generous support of the foll owing important partners and sponsors: Underwriting and Assistance a generous endowment fund. Thanks to Bat Conservation and Management, Inc. (Carlisle , PA) for personnel, equipment, vehicles, and Agency Partners Thanks to the Arizona Game and Fish Department, with special help from State Bat Coordinator, Angie McIn tire, for providing personnel, vehicles, supplies, educational materials and services. Special thanks to the USDA Forest Service, Coronado National Forest, for donating printing and binding materials, and services for production of this workshop Course Bo ok and the workshop Curriculum. We also thank the USDI Fish and Wildlife Service and the US Geological Survey for providing educational materials.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International REMAIN ACTIVE IN BAT CONSERVATIO N AND EDUCATION INITIATIVES Subscribe to Bat Research News magazine, $ 15 per volume year (quarterly) or $25 per volume year for institutions. To subscribe, contact: Publisher and Managing Editor, G. Roy Horst, Department of Biology, Potsdam College of S.U.N.Y, Potsdam, NY 13676. Tel. (315) 267 2259. Subscribe to BATLINE, an electronic information exchange network. Anyone with an e mail address can subscribe to this free service. You can find subscription information at: BATS maga zine, BCI membership benefits and information, bat facts, up to date resources for researchers, and more! Participate in the North American Symposium on Bat research; a professional gathering of students, educators, researcher s and other ba t workers. It m eets annually in October. Locations rotate between Canada, the United States, and Mexico. For more information: BCI CONTACT INFORMATION Mailing Address Bat Conservation International, Inc. Post Office Box 162603 Austin, Texa s 78716 Shipping Address Bat Conservation International, Inc. 500 North Capitol of Texas Highway Building 1, Suite 200 Austin, Texas 78746 Telephone: 512.327.9721 FAX: 512.327.9724 E mail: Website: © 20 11 , Bat Conservation International


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International TABLE OF CONTENTS Introduction : The World of Bats ........................................................................................................... ..................... .. 1 Bats of the United States and Canada........ ............................................................................................ . 4 Status of Bats in the United States.......................................................................................... ............... .5 Status of U.S. Bat s ........................................................................................................................... .... ..8 Bats of Arizona and their Status ...................................................................................... .... ..................9 Bat Anatomy.................................................................................................................. ........... . ......... ..10 Measurements Used in Species Identification Keys ..................................... ............................ . ... . ...... .11 Common Measurements of U.S. and Canadian Bat Species............................................................... .12 Key to the Bats of Arizona ................................................................... ................. ..............................14 Key to the Myotis of Arizona ................................................................................ ..............................16 Habitat Assessment and Management: Roosting Patterns of U.S. and Canadian Bat Species.......................................................................... .17 Variation in the Cave Environment and its Biological Implications................................................... .19 Guidelines for the Protection of Bat Roosts .......................................................... ..............................36 On Cave Gates ............................................................................................................... ..................... .39 Does Com petition for Roosts Influence Bat Distribution in a Managed Forest? .. ..............................55 Potential Effects of Livestock Water Trough Modifications on Bats in Nor thern Arizona ................60 Threats to Survival: Cave Conservation: Special Problems of Bats ...................................................... ..............................68 Thermal Requirements During Hibernation .......................................................... ..............................73 Ecological Impacts of Wind Energy Developments on Bats............................................................ ...83 Bat White nose Syndrome: An Emerging Fungal Pathogen ................................. ..............................96 Importance of Bats: Food Habits of U.S . and Canadian Bat Species ................................................... .............................104 Prey Selection in a Temperate Zone Insectivorous Bat Community.................... .............................106 Bats and Integrated Pest Manag ement.................................................................. .............................118 Economic Value of the Pest Control Service Provided by Brazilian Free tail ed Bats......................120 Bats Limit Arthropods and Herbivory in a Trop ical Forest ............................................................ . .126 Bats Limit Insects in a Neotropical Agroforestry System ................................... .............................128 Capture and Study Techniques: Placement of Nets for Ba ts: Effects on Perceived Fauna ..................................... .............................130 Mist Net Effort Required to Inventory a Forest Bat Species Assemblage ........... .............................133 An Improved Trap for Bats ............... ................................................................... .............................141 A Comparison of Mist Nets and Two Designs of Harp Traps for Capturing Bat s............................144 Comparison of Sampling Methods for Inventory of Ba t Communities ............... .............................149 Temporal Variation in Activity of Bats and the Design of Echolocation monitoring Studies..........158 Transmitter Attachment for Small Insectivorous Bats (< 30 g) ............................... .........................16 6 Injuries to Plecotus townsendii from Lipped Wing Bands................................... .............................167 Education and Public Health: Educational Guidelines...................................................... ............................................................... .170 Bats in the Classroom: A Conceptual Guide for Biology Teachers .................... .............................174 Rabies ................................................................. ................................................. .............................17 9


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Bats & The Public: On line, Up to the minute Resources on the BCI Website . .............................18 4 Artificial Roosts: Use of Artificial Roosts by Forest dwelling Bat s in Northern Arizona .............. .............................18 5 Creating Bat friendly Bridges and Culverts ........................................................ . .............................191 Artificial Roosts and Other Conservation Initiatives f or Bats: On line Resources from BCI ...........194 Reference Materials: Glossary of Scientific Names Given to Bats ........................................................ .............................195 Acoustic Inventory Data Sheet ....................... ...................................................... .............................196 Bat Capture Data Form................................................................................... . ...... .............................197 Instructions for Filling out Bat Capture Data Forms ... . .................................. . ...... .............................19 8 Bat Capture Data Form: Myotis californicus vs. Myotis ciliolabrum . ................... .............................200 Recommended Survey Methods Matrix for Western bat Species ........................ .............................201 Additional Reference Materials, Complete Capture Reports from Past BCI Workshops, and bsite Stay Involved in Bat Conservation


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 1 The World of Bats By: Merlin D. Tuttle Excerpted and updated with permission from University of Texas Press, 1997 (Rev. Ed), pp. 5 16. Illustrations by David Chapma n, Copyright © 1998 From Discover Bats! Bat Conservation International ORIGINS AND RELATIVES Bat fossils have been found that date back approximately 50 million years, but, surprisingly, the bats of that ancient period very closely resembled those we kno w today. Thus, bats have been around for a very long time. Before humans began to affect their numbers, bats were extremely abundant. In some places they probably dominated the night skies just as passenger pigeons filled the daytime skies of the eastern U nited States prior to the nineteenth century. In the evolution of played essential roles; their loss today could compromise the health and stability of our environment. Bats are mammals, but such uniq ue ones that scientists have placed them in a group of their own, the Chiroptera, which means hand wing. All living bat species fit into one of two major groups, the Microchiroptera or the Megachiroptera. Members of the latter group are commonly referred t o as flying foxes because of their fox like faces. They are found only in the Old World tropics, while the Microchiroptera, which are highly varied in appearance, occur worldwide. Like humans, bats give birth to poorly developed young and nurse them from a pair of pectoral breasts. In fact, Linnaeus, the father of modern taxonomy, was so impressed by the similarities between bats and primates (lemurs, monkeys, apes, and humans) that he originally scientists generally agree that primates and bats share a common shrew like ancestor, but belong to separate groups. A heated debate was recently triggered by the discovery that flying foxes, primates, and flying lemurs share a unique brain organization. (Flying lem urs, apparently close relatives of the true lemurs of Madagascar, are a poorly known group of cat size gliding mammals that live in the Indonesian region and, like bats, are in a separate group of their own, the Dermoptera.) Did both the Micro and Megachi roptera come from a single, shrew like, gliding ancestor, or did the flying foxes evolve separately from primates? If the latter notion is correct, are their unique brain characteristics sufficient reason for reclassifying flying lemurs and flying foxes as primates? The issue remains unresolved, but most scientists agree that bats are far more closely related to primates than to the rodents with which they often are linked in the public mind. DIVERSITY AND DISTRIBUTION Over twelve hundred kinds of bats a mount to nearly a quarter of all mammal species, and they are found everywhere except in the most extreme desert and polar regions. Over forty species live in the United States and Canada, but the majority inhabit tropical forests where,


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 2 in total number of species, they sometimes outnumber all other mammals combined. Bats come in an amazing variety of sizes and bumblebee bat of Thailand, weighs less than a penny, but some flying foxes of the Old World tropic s have wingspans of up to 6 feet. The big eyed, winsome expressions of flying foxes often surprise people who would never have thought that a bat could be attractive. Some bats have long angora like fur, ranging in color from bright red or yellow to jet bl ack or white. One species is furless, and another even has pink wings and ears. A few are so brightly patterned that they are known as butterfly bats. Others have enormous ears, nose leaves, and intricate facial features that may seem bizarre at first, but become more fascinating than strange when their sophisticated role in navigation is explained. NAVIGATION AND MIGRATION Like dolphins, most bats communicate and navigate with high frequency sounds. Using sound alone, bats can and in total darkness they can detect obstacles as fine as a human hair. The sophistication of their unique echolocation systems surpasses current scientific understanding and on a watt by watt, ounce per ounce basis has been estimated to be literally bill ions of times more efficient than any similar system developed by humans. In addition, bats are not blind and many have excellent vision. In temperate regions, cold winters force bats to migrate or hibernate. Most travel less than 300 miles to find a suit able cave or abandoned mine, where they remain for up to six months or more, surviving solely on stored fat reserves. However, several species are long distance migrators, traveling from as far north as Canada to the Gulf states or Mexico for the winter. A few species can survive short term exposure to sub freezing temperatures, enabling them to over winter in cliff faces or in the outer walls of buildings. Typically, bats are very loyal to their birthplaces and hibernating sites, but how they find their way over the long distances that often exist between their hibernating and summer caves remains largely a mystery. It appears that some orient visually, using mountain ranges and other landmarks to guide them, but a few are known to have found their way ev en when blinded. Information about how to find obscure sites, such as small cave entrances, apparently is passed on from generation to generation. COURTSHIP, REPRODUCTION, AND LONGEVITY Most bats that live in temperate regions, such as the United States and Canada, mate in the fall just before entering hibernation. Some sing, do wing displays, and perhaps more to attract mates, but little is known about the details. Ovulation and fertilization (through sperm that have been dormant in the female reproducti ve tract since the previous fall) occur in the spring as females emerge from hibernation. Pregnant females then move from hibernating sites (hibernacula) to warmer roosts, where they form nursery colonies. Birth occurs approximately a month and a half to t wo months later. The young grow rapidly, often learning to fly within three weeks. While they are being reared, males and non reproductive females often segregate into separate groups called bachelor colonies. Some tropical bats engage in elaborate courts hip displays. For example, male epauletted bats sing and flash large fluffs of white shoulder fur to attract mates, while male crested bats perform a spectacular display by expanding long hairs on top of the head, similar to a peacock spreading its tail. A t least a few tropical species are monogamous, sharing hunting and family duties. Vampire bats even adopt orphans, unusual for any wild animal. Bats are, for their size, the slowest reproducing mammals on earth. On average, mother bats rear only one youn g per year, and some do not give birth until they are two or more years old. Exceptionally long lived, a few survive for more than 34 years. FEEDING AND ROOSTING BEHAVIOR


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 3 Although 70 percent of bats eat insects, many tropical species feed exclusively on f ruit or nectar. A few are carnivorous, hunting small vertebrates, such as fish, frogs, mice, and birds. Despite their notoriety, vampire bats make up only a small portion of all bats (there are only three species), and they live only in Latin America. With the exception of three species of nectar feeding bats that live along the Mexican border of Arizona and Texas, all bats in the United States and Canada are insectivorous. Bats can be found living in almost any conceivable shelter, though they are best kn own for living in caves. Many species that now live mostly in buildings do so, at least in part, because they have few alternatives. Tropical species occupy a wider range of roost sites than temperate species. For example, some make tent like roosts by bit ing through the midribs of large leaves, and several species have suction discs on their wings and feet that enable them to live in the slick walled cavities formed by unfurling leaves, such as those of the banana plant. Others live in animal burrows, flow ers, termite nests, and even in large tropical spider webs. Despite the wide variety of roosts used by bats, many species have adapted to living in roosts of only one or a few types and cannot survive anywhere else. ECOLOGICAL AND ECONOMIC VALUE Worldwide , bats play essential roles in keeping populations of night flying insects in balance. Just one bat can catch hundreds of insects in an hour, and large colonies catch tons of insects nightly, including beetle and moth species that cost American farmers and foresters billions of dollars annually, not to mention mosquitoes in our backyards. The 20 million free tailed bats from Bracken Cave in Central Texas eat more than 200 tons of insects in a single mid summer night! Throughout the tropics the seed dispers al and pollination activities of fruit and nectar eating bats are vital to the survival of rain forests, with some bats acting as ecosystems. Many plants bloom at night, using unique odors and sp ecial flower shapes to attract bats. The famous baobab tree of the eastern African savannas is a good example. Only bats approach from below in a organs and achieve pollination. Of course they do so becaus e the plant rewards them handsomely with nectar. This tree is so important to the survival of other kinds of valuable crop plants also rel y on bats for survival. Some of the better known commercial products are fruits such as bananas, breadfruit, avocados, dates, figs, peaches, and mangoes. Others include cloves, cashews, carob, balsa wood, kapok (filler for life preservers), and even tequil a. Most of the plants from which these products come are now commercially cultivated, but the maintenance of wild ancestral stocks is critically important. They are the only source of genetic material for developing disease resistant strains, rejuvenating commercial varieties, and for producing new, more productive plants in the future. We already know that more than 300 plant species in the Old World tropics alone rely on the pollinating and seed dispersal services of bats, and additional bat plant relat ionships are constantly being discovered. These plants provide more than 450 economically important products, valued in the hundreds of millions of dollars annually. Just one, the durian fruit of Southeast Asia, sells for $120 million each year and relies almost exclusively on flying foxes for pollination. Other products from these 300 plus plants include 110 for food and drinks, 72 for medicines, 66 for timber and wood derivatives, 34 for ornamentals, 29 for fiber and cordage, 25 for dyes, 19 for tannins, 11 for animal fodder, and 8 for fuel. Numerous additional bat dependent plants of the New World tropics are of similarly great importance. The value of tropical bats in reforestation alone is enormous. Seeds dropped by bats can account for up to 95 percen t of forest re growth on cleared land. Performing this essential role puts these bats among the most important seed dispersing animals of both the Old and New World tropics. Studies of bats have contributed to the development of navigational aids for the blind, birth control and artificial insemination techniques, vaccine production, and drug testing, as well as to a better understanding of low temperature surgical procedures. Unfortunately, however, careless exploitation of bats has sometimes decimated lo cal populations, and careful management planning is required.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 4 Bats of the United States and Canada (46 Species ) FAMILY MORMOOPIDAE Mormoops Mormoops megalophylla faced bat FAMILY PHYLLOSTOMIDAE Artibeus Artibeus jamaicensis Jamai can fruit eating bat Choeronycteris Choeronycteris mexicana Mexican long tongued bat Leptonycteris Leptonycteris nivalis Mexican long nosed bat Leptonycteris yerbabuenae ( sanborni, curasoae in part) lesser long nosed bat Macrotus Macrotus califor nicus California leaf nosed bat FAMILY VESPERTILIONIDAE Antrozous Antrozous pallidus pallid bat Corynorhinus (Plecotus) Corynorhinus rafinesquii eared bat Corynorhinus townsendii eared bat Eptesicus Eptesicus fusc us big brown bat Euderma Euderma maculatum spotted bat Idionycteris Idionycteris phyllotis eared bat Lasionycteris Lasionycteris noctivagans silver haired bat Lasiurus Lasiurus blossevillii western red bat Lasiurus borealis east ern red bat Lasiurus cinereus hoary bat Lasiurus ega southern yellow bat Lasiurus intermedius northern yellow bat Lasiurus seminolus Seminole bat Lasiurus xanthinus western yellow bat Myotis Myotis auriculus southwestern myotis Myotis austrori parius southeastern myotis Myotis californicus California myotis Myotis ciliolabrum western small footed myotis Myotis evotis long eared myotis Myotis grisescens gray myotis Myotis keenii Myotis leibii eastern small footed myoti s Myotis lucifugus little brown myotis Myotis occultus Arizona myotis Myotis septentrionalis northern (long eared) myotis Myotis sodalis Indiana myotis Myotis thysanodes fringed myotis Myotis velifer cave myotis Myotis volans long legged myot is Myotis yumanensis Yuma myotis Nycticeius Nycticeius humeralis evening bat Parastrellus Parastrellus ( formerly Pipistrellus) hesperus canyon bat Perimyotis Perimyotis ( formerly Pipistrellus) subflavus tri colored bat FAMILY MOLOSSIDAE Eumops Eumops floridanus Florida bonneted bat Eumops perotis greater bonneted bat Eumops underwoodi Molossus Molossus molossus Nyctinomops Nyctinomops femorosaccus pocketed free tailed bat Nyctinomops ma crotis big free tailed bat Tadarida Tadarida brasiliensis Mexican free tailed bat


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 5 Status of Bats in the United States by Michael J. Harvey American Caves , Vol. 10, No. 1: Pages 10 13, Spring/Summer 1997. Of th e forty five U.S. bat species, six wholly or partially (i.e., certain subspecies) are considered endangered (in danger of extinction throughout all or a significant portion of their range) by the US. Fish and Wildlife Service as well as most state wildlife agencies. Five of the six are cave dwellers. Twenty additional entire species or subspecies, mostly cave bat species, are considered to be of special concern. Several of the remaining species, especially cave bats, also appear to be declining in numbers. Because of concern for the welfare of endangered, as well as other bat species, the necessity for protection and management of these species and their most critical habitat is evident. Before management recom mendations could be formulated, studies had to be conducted to obtain pertinent data concerning distribution, status, and ecology of these species. Studies were initiated by several state and federal agencies. Primary objectives were to determine distribution and status of endangered and special concer n species, to obtain information concerning various aspects of their ecology, and to formulate management recommendations. Gathering data about other non endangered bat species was an additional objective. Techniques used included searching caves previousl y known to be inhabited by bats and at tempting to locate additional bat caves. In addition to identifying important bat caves, sampling for the presence of bats was done by mist netting or by using bat traps at numerous locations. Mist nets are large (up to 3 x 18 m; 10 x 60 ft) nets made of very fine thread, which are used to capture flying bats. Bat traps consist of two frames a few inches apart over which are strung very thin vertical wires, one inch (2.5 centimeters) apart. Bats flying into a trap det ect and avoid the first set of wires, then hit the second set of wires and fall into a collecting bag. Observations of bat activity were made using night vision (or starlight) scopes and with ultrasonic bat detectors, devices that render ultrasonic bat cri es audible to human ears. On some occasions, bats were fitted with small vials containing a chemical light substance (Cyalume) to study flight behavior and to determine foraging habitat and movements. Some bats were also studied by fitting them with tiny r adio transmitters and tracking their movements with directional antennae and radio receivers. To study migration and movement patterns, numerous bats were banded with colored, celluloid, numbered, wing bands or with numbered metal bands provided by the U.S . Fish and Wildlife Service. Temperature and humidity at roost sites were also obtained. Other data gathered included information on sex ratios, reproduction, swarming, longevity, food habits, mortality, effects of cave gates and fences, and various other behavioral and ecological data. Long term monitoring programs were initiated to determine population trends over time and to ascertain the effectiveness of management measures already initiated. The U.S. Fish and Wildlife Service has had Recovery Plans pre pared for endangered bats by Recovery Teams comprised of bat experts. Certain protective management measures have already been taken, as recommended in the Recovery Plans. These include gating or fencing important bat caves and placing of warning signs at other caves to minimize human disturbance to bat colonies. Signs placed at selected cave entrances tell what endangered bat species inhabit the cave, the season when they are present, information concerning bats' beneficial nature, and adverse effects of disturbing bat colonies. Signs also point out that entering these caves during restricted times is a violation of the Federal Endangered Species Act, punishable by fines of up to $50,000 for each violation. Several state and federal agencies and organizati ons are now actively involved in bat conservation. These include state wildlife agencies, U.S. Fish and Wildlife Service, U.S. Forest Service, National Park Service, Bureau of Land Management, U.S. Army Corps of Engineers, Tennessee Valley Authority, state parks, natural heritage commissions, Nature Conservancy, National Speleological Society, Cave Research Foundation, Bat Conservation International, and the American Cave Conservation Association. Members of several other organizations and numerous private landowners and other individuals are also involved. All are to be commended for their efforts. Information concerning the location of additional important bat caves is needed as part of the continuing bat conservation effort. Individuals with knowledge of caves containing bat colonies should contact appropriate wildlife agency personnel.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 6 ENDANGERED CAVE BATS Leptonycteris yerbabuenae , Lesser Long nosed Bat A resident of desert scrub country, the lesser long nosed bat occurs in the southwestern U.S. to s outhern Mexico. It is colonial, occupying mines and caves at the base of mountains where the alluvial fan supports agaves, yuccas, saguaros, and organ pipe cacti. Like other leaf nosed bats, it will take flight when disturbed. When launching, it gives seve ral strong wing beats, bringing the body into a horizontal position before releasing its grip. It is an agile flier, and can fly nearly straight up while maintaining a horizontal body position. Flight is rapid and direct, showing none of the fluttering mov ements char acteristic of most insectivorous bats. It emerges late in the evening, about one hour after sundown. The long tongue, covered with hair like papillae toward the tip, is well adapted for feeding at flowers. These bats may land on the flowering stalk of agaves and insert their long snouts into each blossom. After feeding, the stomach is so distended that the bat appears to be in late pregnancy. When the stomach is filled, they retire to a night roost where they hang up and rest. Nectar, pollen, a nd insects are consumed, but fruits are eaten after the flowering season is past. One baby is born in late May or June. Maternity colonies may number into the thousands of individuals. This bat appears to be locally common in southeastern Arizona. Leptony cteris nivalis , Mexican Long nosed Bat This bat is found from the Big Bend region of Texas, southward across most of Mexico to central Guatemala. It is a colonial cave dweller that usually inhabits deep caverns, but also can be found in mines, culverts, ho llow trees, and unoccupied buildings. It occupies a variety of habitats from high elevation, pine oak woodlands to sparsely vegetated deserts. The muzzle is greatly lengthened and this bat has a long protrusive tongue, which is attached to the posterior st ernum. There are rows of hair like projections that cover the area near the tip of the tongue, which aid in acquiring nectar. It emerges relatively late in the evening to feed. It is an agile flyer, capable of quick maneuvering and relatively high speed fl ight. It makes swooshing sounds as it flies and can fly straight up while maintaining a horizontal body position. It feeds primarily on nectar, pollen, insects, and soft, succulent fruits of cactus during the non flowering season. When foraging at agaves, it crawls down the stalk, thrusts its snout into the flowers, and licks nectar from them with its long tongue, which can be extended up to 7.5 centimeters (3 inches) and can reach nectar at the base of the corolla of the flowers. It emerges from the flower s covered with pollen and is an effective pollinator of many cacti, agaves, and other plants. It gives birth to one baby in April, May, or June. It is rare in the United States. Myotis grisescens , Gray Myotis The gray myotis occupies cave regions of Arkan sas, Missouri, Kentucky, Tennessee, and Alabama, with occasional colonies found in adjacent states. Gray myotis are cave residents year round, but different caves usually are occupied in summer and winter. Few have been found roosting outside caves. They h ibernate primarily in deep vertical caves with large rooms acting as cold air traps (5 11°C or 58 77°F). Summer roosts are often in caves with domed ceilings capable of trapping combined body heat from clustered individuals. Because of their specific habit at requirements, fewer than 5% of available caves are suitable for gray myotis. Males and non reproductive females form bachelor colonies in summer. Gray myotis primarily forage over water of rivers and lakes. Moths, beetles, flies, mosquitoes, and mayflie s are important in the diet, but gray myotis also consume a variety of insects. Mating occurs in September and October, and females enter hibernation immediately after mating. Females store sperm through winter and become pregnant after emerging from hiber nation. One baby is born in late May or early June, and begins to fly within 20 25 days of birth. The life span may exceed 14 15 years. About 90% of these bats hibernate in only nine caves making them extremely vulnerable to destruction. Myotis sodalis , I ndiana Myotis The Indiana myotis occupies cave regions in the eastern United States. They usually hibernate in large dense clusters of up to several thousand individuals in sections of the hibernation cave where temperatures average 3 6°C (38 43°F) and wit h relative humidities of 55 95%. They hibernate from October to April, depending on climatic conditions. Females depart hibernation caves before males and arrive at summer maternity roosts in mid May. The summer roost of adult males often is near maternity roosts, but where most spend the day is unknown. Others remain near the hibernaculum, and a few males are found in caves during summer. Between early August and mid September, Indiana myotis arrive near their hibernation caves and engage in swarming and m ating activity. Swarming at cave entrances continues into mid or late October. During this time, fat reserves are built up for hibernation. When pregnant, females eat soft bodied insects; they eat moths when lactating, and moths, beetles, and hard bodied insects after lactation. Males also eat a


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 7 variety of insects. One baby is born in June, and is raised under loose tree bark, primarily in wooded streamside habitat. Life spans of nearly 14 years have been documented. The present total known population is a pproximately 350,000, with more than 85% hibernating at only nine locations making them extremely vulnerable to destruction. Populations continue to decrease in spite of recovery efforts. Corynorhinus townsendii eared bat This species occu rs in western Canada, the western United States to southern Mexico, and as a few isolated populations in the eastern United States. They hibernate in caves or mines where the temperature is 12°C (54°F) or less, but usually above freezing. Hibernation sites in caves often are near entrances in well ventilated areas. If temperatures near entrances become extreme, they move to more thermally stable parts of the cave. They hibernate in clusters of a few to more than 100 individuals. During hibernation, the long ears may be erect or coiled. Solitary bats sometimes hang by only one foot. Maternity colonies usually are located in relatively warm parts of caves. During the maternity period, males apparently are solitary. Where most males spend the summer is unknown. No long distance migrations are known. Like many other bats, they return year after year to the same roost sites. It is believed that they feed entirely on moths. Mating begins in autumn and continues into winter, sperm are stored during winter, and ferti lization occurs shortly after arousal from hibernation. One baby is born in June. Babies are large at birth, weighing nearly 25% as much as their mothers. They can fly in two and a half to three weeks and are weaned by six weeks. Life span may be 16 or mor e years. They are locally relatively common in the western United States, but eastern populations (the Virginia and Ozark big eared bats) are endangered. It is believed that fewer than 12,000 individuals exist in the eastern United States. SUMMARY Bats co mprise an extremely interesting and highly beneficial segment of our fauna. They should be understood and appreciated, not feared and persecuted. Like many wild animals, they sometimes pose public health problems or become nuisances by residing where they are not wanted. However, their benefit as the only major predator of night flying insects greatly outweighs their negative aspects. Although only seven U.S. bat species or subspecies are listed as endangered, most species seem to be steadily declining in n umber, some at a rapid rate. Human disturbance to hibernating and maternity colonies and the all too prevalent attitude that factors in declining bat populations. Habitat destruction and the use of pes ticides and other chemical toxicants have no doubt also taken a heavy toll, not only of bats, but of many other fascinating and beneficial species as well. The steady decline in bat numbers, as well as that of many other species, represents much more than just a decrease in a population of organisms. It reflects a steady decline in our overall quality of life as well.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 8 STATUS OF U.S. BATS Mormoops megalophylla faced Bat M acrotus californicus , California Leaf nosed Bat SC Choeronycteris mexicana, Mexican Long tongued Bat SC Leptonycteris curasoae , Lesser Long nosed Bat L. c. yerbabuenae , Lesser Long nosed Bat END Leptonycteris nivalis , Mexican Long nosed Bat END Arti beus jamaicensis , Jamaican Fruit Bat Myotis auriculus , Southwestern Myotis Myotis austroriparius , Southeastern Myotis SC Myotis californicus , California Myotis Myotis ciliolabrum , Western Small footed Myotis SC Myotis evotis , Long eared Myotis SC Myotis grisescens , Gray Myotis END Myotis keenii Myotis Myotis leibii , Eastern Small footed Myotis SC Myotis lucifugus , Little Brown Myotis Myotis occultus, Arizona Myotis SC Myotis septentrionalis, Northern Long eared Myotis Myoti s sodalis , Indiana Myotis END Myotis thysanodes , Fringed Myotis SC Myotis velifer, Cave Myotis SC Myotis volans, Long legged Bat SC Myotis yumanensis , Yuma Myotis SC Lasionycteris noctivagans , Silver haired Bat Parastrellus ( formerly Pi pistrellus) hesperus , Canyon Bat Perimyotis ( formerly Pipistrellus) subflavus , Tri colored Bat Eptesicus fuscus , Big Brown Bat Lasiurus blossevillii , Western Red Bat Lasiurus borealis , Eastern Red Bat Lasiurus cinereus , Hoary Bat L. c. semotus , Hawai ian Hoary Bat END Lasiurus ega , Southern Yellow Bat Lasiurus intermedius , Northern Yellow Bat Lasiurus seminolus , Seminole Bat Lasiurus xanthinus, Western Yellow Bat Nycticeius humeralis , Evening Bat Euderma maculatum , Spotted Bat SC Idionycter is phyllotis , Allen's Big eared Bat SC Corynorhinus rafinesquii cared Bat SC Corynorhinus townsendii eared Bat C. t. virginianus , Virginia Big cared Bat END C. t. ingens , Ozark Big cared Bat END C. t. pallescens , Western Big eared Bat SC C. t. townsendii eared Bat SC Antrozous pallidus , Pallid Bat Molossus molossus Tadarida brasiliensis , Mexican Free tailed Bat Nyctinomops femorosaccus, Pocketed Free tailed Bat Nyctinom ops macrotis , Big Free tailed Bat SC Eumops floridanus , Florida Bonneted Bat SC Eumops perotis , Greater Bonneted Bat E.p. californicus , Western Mastiff Bat SC Eumops underwoodi


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 9 Bats of Arizona and their Status 1 (28 Spec ies) FAMILY MORMOOPIDAE Species Name USFWS USFS BLM AGFD WBWG IUCN Mormoops megalophylla Medium LR: lc FAMILY PHYLLOSTOMIDAE Species Name USFWS USFS BLM AGFD WBWG IUCN Choeronycteris mexicana SC Sensitive Sensitive Threatened High LR: nt Leptonycteris yerbabuenae Endangered Endangered Endangered Endangered High VU: A1c Leptonycteris nivalis * Endangered Endangered Endangered Not listed High EN: A1c Macrotus californicus SC Sensitive Sensitive Candidate High VU: A2c FAMILY VESPERTILIONIDAE Species Name USFWS USFS BLM AGFD WBWG IUCN Antrozous pallidus Low LR: lc Corynorhinus townsendii SC Sensitive High VU: A2c Eptesicus fuscus Low LR: lc Euderma maculatum SC Sensitive Sensitive Candidate Medium LR: lc Idionycteris phyllotis SC Sensitive Sensitive High LR: lc Lasionycteris noctivagans Medium LR: lc Lasiurus blossevillii Sensitive Candidate High LR: lc Lasiurus cinereus Medium LR: lc Lasiurus xanthinus Sensitive Can didate High LR: lc Myotis auriculus Medium LR: lc Myotis californicus Low LR: lc Myotis ciliolabrum SC Sensitive Medium LR: lc Myotis evotis SC Sensitive Medium LR: lc Myotis occultus SC Sensitive Medium LR: lc Myotis thys anodes SC Sensitive Medium LR: lc Myotis velifer SC Sensitive Medium LR: lc Myotis volans SC Sensitive Medium LR: lc Myotis yumanensis SC Low LR: lc Parastrellus hesperus Low LR: lc FAMILY MOLOSSIDAE Species Name USFWS USFS BLM AGFD WBWG IUCN Eumops perotis SC Medium LR: lc Eumops underwoodi SC Sensitive Medium LR: nt Nyctinomops femorosaccus Sensitive Medium LR: lc Nyctinomops macrotis SC Sensitive Medium LR: lc Tadarida brasiliensis Low LR: nt 1 Sources for status determination are as follows: all former Category 2 species. These are species whose conserva tion status may be of concern to the US Fish and Wildlife Service, but do not have official status. USFS = U.S. Forest Service (Region 3) Sensitive Species list. Taxa on this list are species proposed for the list currently u ndergoing revision. BLM = Burea AGFD = Arizona Game and Fish Department. In prep. Wildlife of Special Concern in Arizona. Arizona Game and Fish D epartment Publica tion. Phoenix . 32 pp. WBWG = Western Bat Working Group The Western Bat Species: Regional Priority Matrix . High priority species may be imperiled or at risk of imperilment, medium priority indicates a level of concern, but information regarding the species and perceived threats is l acking, and low priority indicates that most of ly. IUCN = The World Conservation Union conservation status. EN=endangered, VU=vuln erable, LR:nt=lower risk, near threatened, LR:lc=lower risk, least concern. Red list (EN and VU) subcategories include A=threshold levels of population reduction either in the past (1) or pred icted for the future (2), c=reduction based on decline in area o f occupancy, extent of occurrence or quality of habitat (Hutson and others 2001). *Historical records of Greater long nosed bats in Arizona refer to L. curasoae . However, records of L. nivalis from the Peloncillo Mountains near the New Mexico/Arizona borde r indicate this species may occur in Arizona. From : Hinman, K.E., nd T.K. Snow ( eds. ) 2003. Arizona Bat Conservation Strategic Plan . Nongame and Endangered Wildlife Program Technical Report 213. Arizona Game and Fish Department, Phoenix.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 10 Bat Anatomy After: Schmidly, David J. The Bats of Texas . Texas A&M University Press, College Station, 188 pages. (Drawing by Christine Stetter)


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 11 Measurements Used in Species Identification Keys Wing of a big brown bat ( drawn semi diagrammatically), labeled to show names of external parts and measurements used in key to Texas bats. The inset drawing is an enlargement of the metacarpal phalangeal joint in a juvenile (A.) and an adult (B.) bat. After: Schmidly, David J. The Bats of Texas . Texas A&M University Press, College Station, 188 pages. (Drawing by Christine Stetter)


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 12 Common Measurements of U.S. and Canadian Bat Species Adapted with permission from: Lollar, A. and B.A.S. French. 1998. Captive Care and Medical Refe rence for the Rehabilitation of Insectivorous Bats , 2002 (2 nd Ed.). Bat World Publications, Mineral Wells, TX. 340 pages. FAMILY MORMOOPIDAE Species Name Common Name WT (g) FA (mm) WS (mm) SOURCE Mormoops megalophylla faced bat 13 19 51 59 370 1 FAMILY PHYLLOSTOMIDAE Species Name Common Name WT (g) FA (mm) WS (mm) SOURCE Artibeus jamaicensis Jamaican fruit eating bat 50 60 58 59* 5,6 Choeronycteris mexicana Mexican long tongued bat 10 25 43 45 345 1 Leptonycteris yerbabuenae Lesser l ong nosed bat 18 30 51 56 380 3,2,3 Leptonycteris nivalis Mexican long nosed bat 24 55 60 410 1 Macrotus californicus California leaf nosed bat 12 20 47 55 340 3,2,3 FAMILY VESPERTILIONIDAE Species Name Common Name WT (g) FA (mm) WS (mm) SOURCE Antroz ous pallidus Pallid bat 12 17 48 60 353 1 Corynorhinus rafinesquii eared bat 7 13 40 46 270 1 Corynorhinus townsendii eared bat 7 12 39 48 293 1 Eptesicus fuscus Big brown bat 13 20 42 51 325 1 Euderma maculatum Spotted bat 16 20 48 51 365 1 Idionycteris phyllotis eared bat 8 16 43 49 310 350 3,2,2 Lasionycteris noctivagans Silver haired bat 8 12 37 44 289 1 Lasiurus blossevillii Western red bat 10 15 39 42 295 1 Lasiurus borealis Eastern red bat 10 15 35 45 312 1 Lasiurus cinereus Hoary bat 20 35 46 58 400 1 Lasiurus ega Southern yellow bat 10 15 45 48 345 1 Lasiurus intermedius Northern yellow bat 18 24 45 56 370 1 Lasiurus seminolus Seminole bat 10 15 35 45 300 1 Lasiurus xanthinus Western yellow ba t 10 15 45 48 335 355 8,2,2 Myotis auriculus Southwestern myotis 6 9 37 41 270 8,2,2 Myotis austroriparius Southeastern myotis 5 7 36 41 254 1 Myotis californicus California myotis 3 5 29 36 220 1 Myotis ciliolabrum Western small footed myotis 4 5 30 3 6 242 1 Myotis evotis Long eared myotis 4.2 8.6 36 41 275 4,2,2 Myotis grisescens Gray myotis 7.9 13.5 40 46 275 300 7,2,2 Myotis keenii 4 5.9 32 39 228 258 4,2,2 Myotis leibii Eastern small footed myotis 4.1 5.5 30 36 212 248 7,2,2 Myot is lucifugus Little brown myotis 7 9 34 41 239 1 Myotis occultus Arizona myotis 7 9 34 41 239 1 Myotis septentrionalis Northern myotis 5 9 32 39 241 1 Myotis sodalis Indiana myotis 7 7.5** 35 41 240 267 7,2,2 Myotis thysanodes Fringed myotis 6 11 39 46 285 1 Myotis velifer Cave myotis 15 37 47 296 1 Myotis volans Long legged myotis 5 9 35 41 267 1 Myotis yumanensis Yuma myotis 4 6 32 38 225 1 Nycticeius humeralis Evening bat 5 7 33 39 263 1 Parastrellus hesperus Canyon bat 3 6 27 33 190 1 Perimyot is subflavus Tri colored bat 4 6 31 35 237 1


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 13 FAMILY MOLOSSIDAE Species Name Common Name WT (g) FA (mm) WS (mm) SOURCE Eumops floridanus Florida bonneted bat 30 47§ 57 66 470 7,2,2 Eumops perotis Greater bonneted bat 65 72 82 550 1 Eumops underwoodi Un 53 61 65 77 500 540 1 Molossus molossus 12 15 36 41 5,5 Nyctinomops femorosaccus Pocketed free tailed bat 10 14 44 50 345 1 Nyctinomops macrotis Big free tailed bat 24 30 58 64 426 1 Tadarida brasiliensis M exican free tailed bat 11 14 36 46 301 1 This table is intended only as a very general guideline. The information was derived from a diversity of sources including so me compiled from regional data only. For detailed information on these species, see Kunz (In press.) and Tuttle (In press.). For bats found in the state of Texas, information was taken from (1) Schmidly, 1991. For bats not found in the state of Texas, information was taken from: (2) Barbour and Davis, 1969, (3) Nowak, 1994, (4) Nagorsen and B righam, 1993; (5) Emmons, 1990; (6) Eisenberg, 1989; (7) Mammalian Species Accounts; (8) Personal communications with researchers. *58.18mm mean for males; 58.89mm mean for females. **7.1g average winter weight for males; 7.4 7.5g average winter weight fo r females. § There is one record of 55.4g for a pregnant female of this species. References Barbour, R.W. and W.H. Davis. 1969. Bats of America . University Press of Kentucky, Lexington, 286 pages. E isenberg, J.F. 1989. Mammals of the Neotropics The Northern Neotropics, Volume I: Panama, Columbia, Venezuela, Guyana, Suriname, French Guiana . University of Chicago Press, Chicago. 449 pages. Emmons, L.H. 1990. Neotropical Rainforest Mammals: A Field Gu ide . University of Chicago Press, Chicago. 281 pages. Nagorsen, D.W., and R.M. Brigham. 1993. Bats of British Columbia . Vancouver; Royal British Columbia Museum, University of British Columbia Press. 164 pages. Nowak, R.M. 1994. . Johns Hopkins University Press, Baltimore, MD, 287 pages. Schmidly, D.J. 1991. The Bats of Texas . Texas A&M University Press, College Station, 188 pages.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 14 Key to the Bats of Arizona A millimeter ruler is required in order to use this key. Select the app ropriate alternative from each couplet (starting with 1a and 1b ). Follow the number for the next pair of choices at the end of each statement, repeating the process until a name is reached instead of a number. Ear length is measured from the notch at the b ase of the ear. Forearm lengths (FA) are measured from wrist to elbow. Information enclosed in parentheses is helpful but not essential. 1a . Nose leaf present ................................ ................................ ................................ ................................ ................................ .............................. 2 1b . Nose leaf absent ................................ ................................ ................................ ................................ ................................ ............................... 5 2a . Ear length greater than 25 mm (FA 48 53mm) ................................ ................................ ................................ .............. Macrotus californic us 2b . Ear length less than 17 mm ................................ ................................ ................................ ................................ ................................ .............. 3 3a . Short tail easily visible, FA 43 48mm (very long nose, gray to grayish brown fur) ................................ ................... Choeronycteris mexicana 3b . No tail visible, FA 51 60mm (moderately long nose, brown to reddish brown fur (adults only)) ................................ ................................ ... 4 4a . Third finger 92 102 mm, last digit of th ird finger 10 12mm, no fringe of hair on rear edge of tail membrane, body fur short and dense (FA 51 56mm) ................................ ................................ ................................ ................................ ................................ Leptonycteris yerbabuenae 4b . Third finger 106 115 mm, last digit of third finger 16 19mm, fringe of hair on rear edge of tail membrane (FA 55 60mm) Leptonycteris nivalis 5a . Distinctive leaf like folds on chin stretching from ear to ear, tail projecting 10mm or more above tail membrane, exiting near middle (eyes appear to be located inside roundish ears, FA 51 59 mm) ................................ ................................ ........................... Mormoops megalophylla 5b . No leaf like folds on chin, tail completely encased by tail membrane or extending beyond it but never exiting from middle of membrane ... 6 6a . Tail extends one third or more beyond rear edge of membrane ................................ ................................ ................................ ...................... 25 6b . Tail never e xtends more than barely beyond rear edge of membrane ................................ ................................ ................................ ............... 7 7a . Ear length 25mm or more ................................ ................................ ................................ ................................ ................................ .................. 8 7b . Ear length less than 25mm ................................ ................................ ................................ ................................ ................................ .............. 11 8a . Conspicuous pair of white spots on shoulders and one on rump, contrasting w/ black dorsal fur (FA 48 51mm) ........... Euderma maculatum 8b . La cking white dorsal spots on shoulders and rump ................................ ................................ ................................ ................................ ........... 9 9a . Dorsal fur lighter at base (pale blond) than tips (brown); pale translucent ear 25 33mm long; FA 50 55mm ...................... Antrozous pallidus 9b . Dorsal fur darker at base than tips ................................ ................................ ................................ ................................ ................................ ... 10 10a . L umps on nose on each side of muzzle; no pair of leaf like structures projecting f orward over face (FA 40 45mm) Corynorhinus townsendii 10b . No lumps on nose , prominent pair of leaf like structures projecting forward over face (FA 42 49mm) ........................ Idionycteris phyllotis 11a . At least anterio r half of dorsal surface of tail membrane heavily furred ................................ ................................ ................................ ....... 12 11b . Dorsal surface of tail membrane mostly naked or very scantily furred ................................ ................................ ................................ ......... 15 12a . Distinct white patches of fur at dorsal bases of thumbs and often on shoulders, dorsal surface of tail membrane f ully furred ..................... 13 12b . No white patches of fur at dorsal bases of thumbs or on shoulders, dorsal surface of tail membrane ranging from half to ful ly furred ....... 14 13a . Light colored ear distinctively edged in black; FA 46 58mm; dorsal hairs dark gray, tipped wit h a broad band of white (giving hoary colored appearance) ................................ ................................ ................................ ................................ ............................... Lasiurus cinereus 13b . Light colored ear never edged in black; FA 35 45mm; dorsal hairs never dark gray, tipped with broad bands of white (though may be white frosted); fur bright reddish in males, tending toward lighter brownish to grayish in females ................................ .. Lasiurus blossevillii* 14a . Body fur yellowish brown, only anterior half of tail membrane fully furred (FA 46 48mm) ................................ ........... Lasiurus xanthinus 14b . Body fur black or dark brown with many hairs distinctly silve r tipped; fur on tail membrane variable, covering at least basal half, sometimes all of dorsal surface (FA 40 43mm ................................ ................................ ................................ ......... Lasionycteris noctivagans 15a . Tragus shor t, blunt, and club shaped (fur very pale brown, contrasts with jet black face and ears, FA 27 33m m) ....... Parastrellus hesperus 15b . Tragus long, pointed or blunt, but never club shaped ................................ ................................ ................................ ................................ ... 16


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 15 16a . First upper premolar at least half as tall as canine (FA 42 51mm, calcar keeled, fur color brown and glossy) ...................... Eptesicus fuscus 16b . First upper premolar less than o ne fourth as tall as canine ................................ ................................ ................................ ............................ 17 17a . Calcar keeled ................................ ................................ ................................ ................................ ................................ ................................ 18 17b . Calcar not keeled ................................ ................................ ................................ ................................ ................................ ........................... 20 18a . Body fur uniformly dark brown or grayish brown with no distinctively darker face mask, FA 38 42mm, ears short (11 14mm) and same color as fur, underside of wing furred to elbow ................................ ................................ ................................ ............................. Myotis volans 18b . Body fur medium to very light tan or reddish brown with clearly darker facemask, FA 29 36mm ................................ .............................. 19 19a . Thumb length greater than 4.2mm, dorsal fur slightly shiny, color pale, sharply contrasting face mask, muzzle length 1.5 times width between nostrils, forehead gently sloped, tip of tail protrudes past tail membrane ................................ ........................... Myotis ciliolabrum 19b . Thumb length less than 4.2mm, dorsal fur dull, color pale, face mask distinctive but often less contrasting, muzzle same le ngth as width between nostrils, forehead steeply sloped, tip of tail does not protrude past tail membrane ................................ ............. Myotis californicus 20a . Distinct fringe of hair on edge of tail membrane (ears darkly pigmented, 12 22mm, belly fur light, FA 39 46mm) ......... Myotis thy sanodes 20b . Fringe absent, no more than occasional scattered hairs on edge of tail membrane ................................ ................................ ...................... 21 21a . Ear length 19mm or more ................................ ................................ ................................ ................................ ................................ ........... 22 21b . Ear length 18mm or less ................................ ................................ ................................ ................................ ................................ ............. 23 22a . Ears, wing, and tai l membranes blackish and opaque; ears 22 24mm, FA 37 40mm ................................ ................................ .. Myotis evotis 22b . Ears, wing, and tail membranes brownish and tra nslucent; ears 19 21mm , FA 37 41mm, face bare especially near eyes . Myotis auriculus 23a . FA 32 36mm, ventral fur with whitish tips ................................ ................................ ................................ ........................ Myotis yumanensis 23b . FA 37 47mm, ventral fur sometimes light er than dorsal but lacking whitish tips ................................ ................................ ........................ 24 24a . Body fur gray to gray brown, dull; ears light colored and match fur , FA 40 45mm, bare patch between shoulder blades ........ Myotis velifer 24b . Body fur brown to reddish brown, glossy; ears always dark er than fu r , FA 36.5 40.5mm ................................ ...................... Myotis occultus 25a . No vertical wrinkles on upper lips, FA 66mm or more ................................ ................................ ................................ ................................ . 26 25b . Deep vertical wrinkles on upper lips, FA 64mm or less ................................ ................................ ................................ ................................ 27 26a . Ear length between 28 32mm, FA 65 74mm, tragus small and rounded, distinc tive long guard h airs on rump ............ Eumops underwoodi 26b . Ear length 36 47mm, FA 73 83mm, tragus broad and square, no obvious long guard hairs on rump ................................ ..... Eumops perotis 27a . Leading edge of ear widening to become club shaped above and behind eye, ears connect at top of nose ................................ ................... 28 27b . Leading edge of ear narrowing to a point above and top of nose (FA 36 46mm) ...... Tadarida brasiliensis 28a . FA 44 50mm ................................ ................................ ................................ ................................ ......................... Nyctinomops femorosaccus 28b . FA 58 64 mm ................................ ................................ ................................ ................................ ................................ Nyctinomops macrotis Illustrations: nectar bat tails, calcars, and free tailed bat ears Christine Setter in Schmidly, D.J., 1991. Bats of Texas, Texas A&M University Press, 188pp.; bat skulls Hall, E.R., 1981. The Mammals of North America, Volume 1 , John Wiley and Sons, New York, 600pp. *The eastern red bat ( Lasiurus borealis ) could possibly be encountered in extreme eastern Arizona, but cannot be reliably distinguished from the red bat ( Lasiurus blossevillii ) based on external characters. The range of these two species overlaps in the Rio Grande valley of TX and possibl y extreme southern NM . y exhibit the remaining diagnostic characters of Myotis californicus and Myotis melanorhinu s , respectively. See the Key to the Myotis of Arizona for additional details. Myotis auriculus often have ears measuring slightly shorter (16 20mm) ; refer to ear and membrane color and opacity in couplet #22 to identify short eared Myotis auriculus from the remaining Myotis species.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 16 Key to the Myotis of Arizona (presented in order of size; from largest to smallest) SPECIES FOREARM LENGTH EAR SIZE (MM) AND COLOR KEELED CALCAR? FUR COLOR ADDED CHARACTERISTICS thysanodes 39 46 mm Long (12 22), dark, though often lighter at base near eye No medium brown fringe of hairs on very edge of tail membrane; ventral fur lighter than dorsal; ears bi colored (lighter at base than at tips) velifer 40 45 mm Short (11 18), pale (match body f ur color), can be variable in length No gray to grayish brown bare patch of skin between shoulder blades sometimes volans 38 42 mm Short (11 14), rounded and dark (match body fur color) Yes chocolate brown as fur; underside of wing furred from elbow to knee 37 40 mm Long (20 24), almost black and opaque (darker than body fur color) russet brown ears, tail, and wing membranes darker than fur color, almos t black, and opaque; sometimes with scant fringe of hairs on tail membrane 36.5 40.5 mm Short (11 16), pointed, dark (darker than body fur color) no (usually) variable shades of glossy brown ears usually slightly to distinctly darker than fur co lor; ventral fur tipped in light brown; looks like a mini big brown bat auriculus 36 39 mm Long (19 21*), pale (match body fur color) and translucent No pale brown to reddish or yellowish brown ears, tail, and wing membranes same color as fur and transluc ent; muzzle bare, especially near eyes yumanensis 32 36 mm Short (12 15), pale (match body fur color) No light or pale brown and dull small bat with big feet (8 10mm); ears same color as fur; ventral fur tipped in white ciliolabrum 31 35.5 mm Short (13 1 6), dark (darker than body fur color) Yes light brown with glossy tips dark black mask; thumb > 4.2mm and chubby; muzzle length 1.5 times width between nostrils; forehead gently sloped; tip of tail protrudes past tail membrane californicus 29 34.5mm Short (8 16), dark (darker than body fur color) Yes light brown with dull tips lighter black mask; thumb < 4.2 mm and skinny; muzzle same length as width between nostrils; forehead steeply sloped; tip of tail does not protrude past tail membrane species, generally no found south of the Mogollon Rim in Arizona * Chiricahua individuals generally have ears measuring slightly shorter; 16 20mm Source : Hoffmeister, D.F. 1986. Mammals of Arizona . University of Arizona Press, Tucson. 602 pages.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 17 Roostin g Patterns of U.S. and Canadian Bat Species Adapted with permission from: Lollar, A. and B.A.S. French. 1998. Captive Care and Medical Reference for the Rehabilitation of Insectivorous Bats, 2002 (2nd Ed.). Bat World Publications, Mineral Wells, TX. 340 p ages. FAMILY MORMOOPIDAE Species Name Common Name Hib? Roosting Patterns Mormoops megalophylla faced bat No hundreds of thousands; in caves, mines, and rarely buildings F AMILY PHYLLOSTOMIDAE Species Name Common Name Hib? Roosting Patterns Artibeus jamaicensis Jamaican fruit eating bat No Cluster in small bachelor groups or groups that include one male & several females. Several of these groups of males & their harems may roost in the same cave. Roost in tree hollows, foliage, & caves. Choeronycteris mexicana Mexican long tongued bat No Do not cluster. Individuals roost about 1 of up to several dozen in caves & mines & occasionally in other shelte rs such as buildings. Leptonycteris yerbabuenae Lesser long nosed bat No Cluster in groups of up to thousands. Generally found during the day in mines & caves, but may rest during the night in open buildings such as barns & carports. Leptonycteris nivali s Mexican long nosed bat No Cluster in groups of up to thousands in mines & caves. Macrotus californicus California leaf nosed bat No Do not cluster. Roost in groups of up to a hundred. Roost in abandoned mines and rock shelters during the day, but can al so roost during the night in open buildings, bridges, mines. FAMILY VESPERTILIONIDAE Species Name Common Name Hib? Roosting Patterns Antrozous pallidus Pallid bat Yes Cluster in groups of up to hundreds. During the day use rock crevices & buildings, but also sometimes in mines, caves, & hollow trees; night roost in rock shelters, open buildings, bridges, & mines. Corynorhinus rafinesquii eared bat Yes Cluster in groups of up to 100 in buildings, behind bark, & in hollow trees, caves, & m ines. Corynorhinus townsendii eared bat Yes Do not cluster. Roost in groups up to 1,000 although generally found in fewer numbers. Roost in caves & mines but are also found in buildings in the west where they night roost in open buildings. Eptesicus fuscus Big brown bat Yes Cluster in groups of up to hundreds; in buildings, bridges, & behind shutters. Have been found roosting in rock crevices, swallow nests, hollow trees, & saguaros. In winter found roosting in caves, mines, quarries, & sto rm sewers. Euderma maculatum Spotted bat Yes Clustering information not available. Roost in cracks & crevices of high cliffs and canyons & possibly caves. Idionycteris phyllotis eared bat § Cluster in groups of up to 100 in caves, rock shelte rs, & mines. Lasionycteris noctivagans Silver haired bat Yes Do not cluster. Solitary; roost behind loose bark, but have been found in buildings, mines, woodpecker holes, & bird nests. Found during migration in open buildings, lumber piles, & fence posts. Lasiurus blossevillii Western red bat Yes Do not cluster. Solitary; roost in tree foliage. Lasiurus borealis Eastern red bat Yes Do not cluster. Solitary; roost in tree foliage. Hibernate in leaf litter. Lasiurus cinereus Hoary bat Yes Do not cluster. Solitary; roost in tree foliage Lasiurus ega Southern yellow bat § Do not cluster. Solitary; roost in leafy vegetation. Lasiurus intermedius Northern yellow bat § Do not cluster although at least females appear to be colonial. Several may roost in same t ree, Spanish moss, & palm leaves. Lasiurus seminolus Seminole bat Yes Do not cluster. Solitary; roost in Spanish moss. Lasiurus xanthinus Western yellow bat Yes Do not cluster. Solitary; roost in mostly dry leafy vegetation. Myotis auriculus Southwester n myotis § Do not cluster. Roost in buildings & caves but also will form colonies of up to 40 or more in tree hollows. Myotis austroriparius Southeastern myotis Yes Cluster in groups of up to thousands. Roost in caves, buildings, & hollow trees, although in winter they are also found in bridges, storm sewers, road culverts, & drain pipes Myotis californicus Californian myotis Yes Cluster in small groups in mines, caves, rock crevices, hollow trees, beneath loose bark, bridges & in open shelters such as ga rages, barns, houses, sheds, & porches.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 18 Species Name Common Name Hib? Roosting Patterns Myotis ciliolabrum Western small footed myotis Yes Cluster in groups of up to 50 in mines, caves, buildings, & sometimes beneath loose bark. Myotis evotis Long eared myotis Yes Do not cluster. Roost in groups of up to 30 in sheds, cabins, beneath bard, & in rock piles. Night roost in caves. Myotis grisescens Gray myotis Yes Cluster in groups of up to thousands mainly in caves, although one maternity colony was found in a storm sewer. Myotis keenii Ye s Do not cluster. Solitary; roost in tree cavities, cliff crevices. Myotis leibii Eastern small footed myotis Yes Cluster in groups of up to 50 in mines, caves & beneath rock slabs in quarries. Maternity colonies found in buildings. Myotis lucifugus Litt le brown myotis Yes Cluster in groups of up to thousands in mines & caves. In summer may also be found in buildings, bridges, & under bark. Myotis occultus Arizona myotis Yes Clustering is unknown. Maternity colonies found in buildings & a bridge. Scant h ibernating records have all been in mines. Myotis septentrionalis Northern myotis Yes Small clusters of up to 30 have been found in maternity colonies; though generally roost singly in mines, caves, buildings, and beneath bark. Myotis sodalis Indiana myo tis Yes Cluster in groups up to 100,000 in caves though maternity colonies use hollow trees. Also found in bridges & beneath loose bark. Myotis thysanodes Fringed myotis Yes Cluster in groups up to 300 in caves, mines, rock crevices, & buildings. Myotis velifer Cave myotis Yes Cluster in thousands in caves, mines, and sometimes buildings. Myotis volans Long legged myotis Yes Cluster in groups of up to hundreds in buildings rock crevices and trees; night roost in mines and caves. Myotis yumanensis Yuma m yotis Yes Cluster in groups of up to thousands in maternity colonies; adult males typically solitary; roost in buildings, under bridges, & in caves & mines. Nycticeius humeralis Evening bat Yes Cluster in groups of up to several hundred in buildings, tree cavities, & behind loose bark. Parastrellus hesperus Canyon bat Yes Do not cluster; relatively solitary, though maternity colonies of up to a dozen bats have been found in rock crevices and behind shutters. Roost in buildings, mines, and caves. Perimyot is subflavus Tri colored bat Yes Do not cluster; relatively solitary, though small maternity colonies of up to 30 individuals have been found. Roost tin Spanish moss, caves, mines, rock crevices and buildings. FAMILY MOLOSSIDAE Species Name Common Name Hi b? Roosting Patterns Eumops floridanus Florida bonneted bat No Clustering unknown. Found in groups of up to 8 individuals. Eumops perotis Greater bonneted bat No Cluster in groups of less than 100 in cliff crevices, rocky canyons, & sometimes buildings Eumops underwoodi No Clustering information unknown. Have been found roosting in small groups in buildings & tile roofs. Molossus molossus No Cluster in hundreds in tree hollows, rock piles & buildings. Nycti nomops femorosaccus Pocketed free tailed bat No Cluster in groups of up to 100 in crevices of rocky out crops & have also been found in tile roofs. Nyctinomops macrotis Big free tailed bat No Clustering information unknown. Roost in rock crevices. Tadari da brasiliensis Mexican free tailed bat No Cluster in groups of up to several million in caves, mines bridges, & buildings. This table is intended only as a very general guideline. § Information not available from reference source used. References Barbo ur, R.W. and W.H. Davis. 1969. Bats of America . University Press of Kentucky, Lexington, 286 pages. Additional information was obtained from: Emmons, L.H. 1990. Neotropical Rainforest Mammals: A Field Guide . University of Chicago Press, Chicago. 281 pages. And species can be found in Kunz (In press.) and Tuttle (In press.)


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 19 Variation in the Cave Environment and its Biological Implications by Merlin D. Tuttle and Diane E. Stevenson National Cave Management Symposium Proceedings , 1977 (R. Zuber, J. Chester, S. Gilbert and D. Rhodes, eds.), pp.108 121. Adobe Press, Albuquerque, NM. INTRODUCTION Constancy of the c ave environment has too often been assumed and emphasized. The most common generalization is that cave temperature varies only near entrances (the variable temperature zone) while that of a cave is constant (the constant temperature zone), with temperature closely approximating the local mean annual surface temperature. Humidity also is often considered to be near saturation and relatively invariant. These generalizations are true in some cases. Certainly, the cave environment is buffered in relation to the outside environment. Overall temporal and spatial variation of temperature and humidity among and within caves, however, is far greater than is generally suspected, and even a small amount of such variation can have great impact on cave faunas (Jegla and Poulson, 1969; Juberthie and Delay, 1973; Delay, 1974; Juberthie, 1975; Poulson, 1975; Tuttle, 1975, 1976; Wilson, 1975; Peck, 1976). Although literature demonstrating considerable variation exists, it is scattered, often in foreign or little known public ations, and sometimes is authored by laymen who publish only once on the subject. Consequently, few individuals, even among biospeleologists, are adequately aware of much of the available literature and its biological implications. Another source of confus ion has been the fact that many authors, while presenting a thorough discussion of one or more variation producing factors, still have opened or concluded with general statements about the constancy of the cave environment. Despite the confusion, in the e xisting literature a variety of factors such as number, size, and position of entrances, passage size, contour and slope, overall cave volume, distance of greatest volume from entrances, amount and seasonal timing of entry of surface water, air flow, and t he annual range of outside temperature have been noted to strongly influence cave temperature and humidity (see Halliday, 1954; Moore and Nicholas, 1964; Plummer, 1964; Cropley, 1965; Geiger. 1965; Peters, 1965; Vandel, 1965; Conn, 1966; Barr, 1968; Daan a nd Wichers, 1968). This paper integrates current knowledge of the cave environment with particular emphasis on air flow and temperature; it presents some of our data on the subject, and discusses the importance of such information to biological research a nd cave management. We believe that familiarity with factors influencing cave environments can be highly useful in biospeleology and cave management, both for the generation of hypotheses and predictions in ecological and distributional studies and for pre dicting the biological uniqueness and potential of any given cave under investigation. METHODS From 1960 to 1975 the senior author visited several hundred caves, primarily in Alabama, Florida, Tennessee, and Virginia, and recorded temperatures at hundreds of winter and summer roosts of the gray bat ( Myotis grisescens). Temperature and humidity readings were recorded using a Bendix Psychron motor driven psychrometer. Since gray bats prefer caves that provide the greatest possible deviations from mean annual surface temperatures, the caves visited during these bat studies provided examples of strikingly different structures and temperature regimes. Many other caves, not used by gray bats, provided additional comparisons. From the winter of 1975 76 through th e winter of 1976 77 a more detailed study of cave temperature was conducted. Thousands of temperature measurements were made in 25 caves and mines from Wisconsin to Florida, in an effort to test the predictions generated incidental to the previous bat stud ies. A quick, accurate temperature measuring device was essential, and a Bailey Thermalert, Model TH 2 digital readout thermometer with a 1 mm diameter thermister probe was used initially. Testing in controlled water baths at temperatures of 0 30°C demonst rated conditions varied with the temperature of the instrument itself, forcing one to carry it beneath one's coveralls and to repeatedly recalibrate against a laboratory tested Wesco mercury thermometer. Though readings could be made in only a few seconds, accuracy with the Thermalert in the Accuracy was greatly improved with the purchase of an IMC Digital Thermometer, Model 2100 (produced by IMC Instruments, Inc., Glendale, Wis. ), with a range of 40° to +250°F. This thermometer proved far more suitable


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 20 for use in caves. It weighed only about 500g, (including batteries), was extremely sturdy, provided reliability over an inst rument temperature range of 0 to 110°F. Using a sensor probe 2.2 mm in diameter, this instrument had a response time of 3 seconds in liquids, 30 seconds or less in air, and from 45 seconds to several minutes (depending on density of solid) for surfaces. Mo st air and wall temperatures reported in this paper were taken with this instrument. Although the data are not presented here, gross daily and seasonal temperature variation was recorded in five cases using Weksler maximum/minimum thermometers, and 24 hou r comparisons between inside and outside temperatures were made using Bacharach Tempscribe recording thermometers, in order to verify our findings. Mean annual surface temperatures (MAST) were obtained from U.S. Department of Commerce (1975a c) publication s. A steel tape or, for the longest distances, a Model 100 Optical Tapemeasure (produced by Ranging Inc., Rochester, N.Y.) were used for cave measurements. Data from only a few representative caves in the study could be included here, but the omitted obse rvations agree well with those selected for discussion. FACTORS THAT INFLUENCE CAVE TEMPERATURE Conduction from Cave Walls If one surface of a very large limestone block were predicted that its int erior temperature would remain very close to (mean annual surface temperature lag in temperature adjustment of approximately 7 days for every foot of depth produces this constancy (Cropley 1965). Cropl ey described as Zone III an area of a cave where isolation from outside conditions is those that are initiated by the conduction of heat from the charact eristic of the constant temperature cave of w ill be seen to be the tendency to gradually return differing air or water temperatures to mean annual surface temperature -the more isolated from outside influences an area is (whether by distance or physical barriers) the more nearly its temperature will approximate MAST. Geographic Location Vandel (1965) listed geographical location and altitude as important factors affecting cave temperature; their major influence is on the range and mean of the annual surface temperature and on standard barometric pres sure. Since the amount of variation from mean annual surface temperature that can be achieved in any given cave is directly proportional to the annual range of surface temperature (see discussion below), caves in tropical regions would be expected to exhib it only the slightest deviations from MAST. To a lesser extent, fluctuations also should be reduced in caves on islands, peninsulas, or even in coastal areas. Within a given area, cave entrances on north versus south slopes, those at different elevations, and those on exposed surfaces versus in deep, protected valleys or sinks will face different means and ranges of surface temperature, which often result in detectable differences in internal temperatures. Another geographic factor is the nature of the geo logical structure present; caves of certain configurations may exist primarily in certain areas. Barr (1961:13) documented the existence of strong geographic tendencies structural tendencies would be expected to be reflected in geographic trends in cave temperature and humidity. This in turn may have important zoogeographic implications. Water Circulation In order for internal temperatures to vary ab ove or below mean annual surface temperature, a cave must have a route of communication with the temperature fluctuations of the outside atmosphere. With cave wall conduction exerting only infinitesimal effect extremely short distances from the surface, th e two main routes of communication are circulation of air and water. Water is most likely to cause deviations from mean annual surface temperatures when it enters directly from the surface in seasons when surface temperatures deviate farthest from the mean annual temperature (Cropley, 1965) or, in rare instances, when it enters from thermal springs (Geiger, 1965). Flooding, as noted by Barr (1968), can produce sudden and pronounced temperature changes and can play a vital role in triggering reproduction of aquatic troglobites (Poulson and Smith, 1969; Jegla and Poulson, 1970). The only until it has flowed a distance sufficient to allow it to reach thermal equilibrium with the cave walls.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 21 Air Circu lation Although exceptions do occur, the impact of air circulation in caves is generally far greater than that of water, if for no other reason than the fact that whereas most known caves have some air circulation (those isolated by water sumps being an ex ception), a much smaller proportion have major water circulation. The four main causes of air circulation affecting cave temperature (see Plummer, 1964) will be discussed. It will be seen that the magnitude and type of impact of all air flow types is overw helmingly determined by the structure (passage configuration) of the cave itself. Barometric pressure -Atmospheric (or barometric) pressure frequently has been cited as a primary factor influencing within cave air movement and temperature fluctuation. A lthough other factors such as solar induced atmospheric tides can produce slight pressure changes (Encyclopedia Britannica, 1975), the relatively greatest fluctuations in barometric pressure at any given altitude are directly the result of temperature chan ges (Moore and Nicholas, 1964). At one location pressure changes can, of course, occur that are due to temperature changes (and the resulting winds) at another distant location, as in the case of changes preceding storm fronts. It is only these non temper ature associated pressure changes that can be discussed meaningfully as barometric pressure influences on cave climate. Changes in the outside air temperature obviously will be accompanied by changes in barometric pressure, since the latter is determined b y the weight of air (colder = heavier). In this paper, however, references to barometric pressure effects will refer only to the non temperature associated changes; temperature associated pressure changes will be considered synonymous with temperature fluc tuation. should exhibit an airflow into the entrance when the outside atmospheric pressure rises, and should emit air impact of this circulation ap pears to be relatively minor (Moore and Nicholas, 1964; Plummer, 1964), especially when compared to that of thermal convection. Its effect certainly is more gradual, transitory, and of less magnitude. Apparently rare cases exist where caves, such as Wind a nd Jewel Caves in South Dakota, have extremely large volumes and generate significant winds through barometric pressure interactions alone (Conn, 1966). Even in these caves, however, internal temperatures probably are affected little, compared to the amoun t that would occur if thermal convection were directly involved. Surface wind. -Surface winds carried into or through caves by their own force may be of some importance in certain instances (Plummer, 1964; Geiger, 1965), but most examples are limited to a cave with a short simple tunnel between its two or more entrances, or to a relatively shallow cave with a large entrance. Plummer (1964) discussed the flow of surface winds through caves with entrances a large distance apart, but points out that in such result from the same difference in barometric pressure be most likely to occur i n a cave shaped like a nearly level tunnel. Resonance. -Schmidt (1959), Eckler (1965), Peters (1965), Moore and Nicholas (1964), Plummer (1964), Porter (1974), Russell (1974) and others have discussed this potential cause of cave "breathing" through a s ingle entrance. The oscillation of air has been attributed to movement of outside air across the entrance, creating shape postulated as suitable for resonance.) Schmidt (see Barr, 1968) also suspected that such resonator effects could explain air flow oscillations olumn of effects similar to surface winds. Although we have not attempted to investigate this phenomenon in any detail, we doubt that the above explanations are of more than rare importance. We have observed both regular and irregular breathing cycles in caves of a variety of structures, and note that oscillations are most likely to occur when outside temperature is fluctuating around or is close to inside temperature. Furthermore, such oscillations o ften persist in the absence of outside wind. When marked outside temperature changes are occurring, as during a storm (for an example, see Eckler, 1965), breathing easily can be explained by thermal convection; Peters (1965) has discussed differing cave st ructures and how they might cause patterns of breathing. Moore and Nicholas (1964) have pointed out that the now


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 22 famous Breathing Cave in Virginia is itself probably a multiple entrance cave dominated by air currents caused by thermal convection. They point to internal complexity of structure as the probable source of breathing and discount the idea that the air flow oscillations are caused by outside wind blowing past its entrance. An alternative explanation (using thermal convection as opposed to reso nance) will be proposed to explain air flow oscillations in caves of Type 3 Thermal convection. -The impact of thermal convection on air movement in and out of caves (and therefore on cave tempera tures) is well known; thermal convection is generally believed to be the most important factor in determining the direction and amount of air exchange with the surface (Halliday, 1954; Plummer, 1964; Geiger, 1965; Peters, 1965; Daan and Wichers, 1968; Port er, 1974; Russell, 1974). The principle of thermal convection in caves is that air escapes (rises) through an upper entrance (or through the top of a single entrance) when it is warmer than the outside air. Conversely, air will escape through a lower entra nce (or through the bottom of a single entrance) when it is cooler than the outside air. The greater the inside to outside temperature gradient, the faster the rate of air movement; flow ceases when the temperatures are the same. (This equilibrium conditio n theoretically should be reached when the outside temperature equals mean annual surface temperature for the area. Different cave types may deviate so markedly from MAST, however, that this equilibrium point may be shifted at times.) Caves can exhibit suc h air flow seasonally, on a daily cycle, or in response to passage of weather fronts. Direction and timing (and to a certain extent, rate) of flow will be determined by the structure of the particular cave. Figure 1. l generally occur when outside temperature is below mean annual Type 1 : Breathes (as indicated by arrows) in winter; stores cold air in summer. Type 2 : Undu lation at A acts as dam inhibiting air flow; temperature relatively constant beyond dam. Type 3 shape often postulated to exhibit resonance; may have pulsing in and out air movement, especially when outside air deviates f rom MAST. See text for alte rnate explanation for the oscillation of air. Type 4 : Strong air circulation from A to B in winter; stores cold air in summer. Type 5 : The reverse of Type 1; warm air enters along ceiling in summer wile air cooled by cave walls flows out along floor. No fl ow in winter. X is a warm air trap, Y stays a relatively constant temperature. Type 6 : Strong air flow from A to B in winter; equally strong air flow in opposite direction in summer. Type 7 : Same as Type 6, with a warm air trap (X) cold air trap (Y), and an area of relatively constant temperature (Z). Distance between and elevational displacement of the entrances are critical factors in the air flow direction in these two cave types; the flow of air (cooled relative to out side temperatures by the cave wall s) down in summer must be strong in order to overcome the tendency for warm outside air to rise into A. Similarly, in winter the by air (now warmer than the outside air due to the MAST effect of the cave walls) rising out of B m ust be strong enough to pull cold air up into A.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 23 Cave Structure and Volume Figure 1 presents seve ral simplified examples of how air circulation works in caves of different structure. Although the number of entrances (including cracks too small for human passage) is an important variable of air circulation, the elevational difference between multiple e ntrances is of primary importance for thermal convection induced temperature variation, as noted by Halliday (1954), Plummer (1964), Geiger (1965), Porter (1974) and others. Negative pressure (as described by Peters, 1965, and Daan and Wichers, 1968) can c reate powerful chimney effects in caves with entrances at different elevations (Figure 1, Types 4, 6 and 7). Halliday also pointed out that other factors, such as irregular, tortuous passages or narrow h ave noted that vertical undulations are especially effective natural dams against the free flow of convection currents (see Figure 1, Type 2). entrance(s) is also of great importance. Distance of a shown to be of importance in determining depth and pattern of air movement in and out of caves where movement is the result of changes in barometric pressure (Conn, 1966). Elevational displacement of cav e volume from an entrance(s), however, is perhaps the most important single factor affecting cave temperature (see Figure 1, Types 1, 4, 5, 6 and 7). As from the entrance, cold air flows downward inside it and is no longer affected by warmer and lighter air. Caves of this type are called sack caves and act as cold reservoirs . . . The opposite thermal effect is obtained when a cave slopes upward from its single ove the entrance can act as warm air traps; cooled air sinks out as warm air rises in. These considerations also apply to cave chambers or passages that extend above or below passages with air flow, as illustrated in Figure 1, Types 5 and 7. Small passage s, in addition to acting as baffles, also dampen temperature fluctuations through their increased cave wall surface to volume ratio -the tendency of the walls to return air to mean annual surface temperature will have maximum effect. udy of ice caves demonstrated not only the importance of having the volume below the lowest entrance but also the necessity of large volume for cold air storage. Halliday, in discussing classical examples of limestone ice caves, repeatedly noted the presen ce of very large volume. He mentioned room sizes of 100 feet by 30 feet, 200 feet by 50 feet, and 300 feet by volume in relat ion to its entrance also could provide an alternate explanation of breathing (air flow oscillations) in caves of Type 3, Figure 1. With its volume approximately equally distributed above and below the entrance, such a cave could be expected to have warm su mmer air entering along the entrance ceiling, with cooled air spilling out along the bottom of the entrance. The reverse flow pattern would occur in winter. If the entrance were sufficiently constricted, however, breathing could be predicted to occur. Ther e no longer would be room for air to move simultaneously in opposite directions; density differentials should lead to a pulsing action. At some point, further increases in entrance passage length and constriction should almost completely inhibit exchange o f inside and outside air in caves of this type. INTERACTION OF CAVE STRUCTURE AND AIR FLOW The following examples of specific caves (see Figures 2 and 3) were taken from our studies in the southeastern United States and will illustrate the extent and natu re of cave structure/air flow interactions. Cave names and locations are withheld because most of the caves discussed contain populations of endangered bats or other cavernicolous faunas. This information will be provided, on request, to those documenting bona fide need. Seasonally Reversing Air Flow Cave number 1 of Figure 2 is an excellent example of Type 6/7, Figure 1. Due to its relatively simple shape, large passage diameter, and 43 meter elevational difference between entrances, air flow is direct an d rapid. We have observed a strong (unmeasured, although probably sometimes exceeding 15 KPH) flow of air exiting the lower entrance and entering the upper on hot summer days, with the reverse being true on cold days in winter. Temperatures at the entrance s in February (Figure 2) show the effect of the cold air entering the low entrance, and warmed air exiting the upper one. Local nearly complete cessation of air flow, either in or out of either entra nce, when the surface temperature is approximately 60°F (15.6°C). Air flow cessation would be expected in this general temperature range due to its proximity to mean annual surface temperature (15.7°C)


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 24 Figure 2. Six southeastern eaves and temperatures (in °C) at some sites for the date indicated near the cave number. Temperatures on ad ditional dates may be given in parentheses. MAST = mean annual surfac e temperature, WL = wall temperature, WT = water temperature. For cave 2 the range of temperatures from January through August is given in parentheses (maximum/minimum; number of degrees in the range). Streams f low from right to left through the lower leve ls of caves 1 and 2. As a consequence of its strong, seasonally reversing air flow, this cave shows the greatest annual range of temperature of any of the hundreds of caves observed in this study. Note the extremes of deviation from MAST at locations H and D in July and February (outside temperatures approximately 34°C and 30°C respectively). Certainly a temperature of 0.6°C 350 m inside an Alabama cave requires exceptionally strong circulation of outside air. This reading, and the high summer temperature at H, are all the more surprising down from K between J and I and up from A to D. Both readings are attributable to the dramatic impact of the negative pressure created by air exiting such a large cave -in summer cool air pours out of the bottom entrance in such a quantity that w arm air is "sucked" in the upper entrance and down the slope. In winter the reverse occurs, when warm (relative to outside) air escaping through the upper entrance creates a partial vacuum which "sucks" cold air into the lower entrance and deep into the ca ve. Lower outside temperatures in January undoubtedly produced below freezing temperatures as far in as site D. Cave number 2 of Figure 2 is a nearly horizontal, two level tube which, according to Barr (1961), ends at point F. Mean annual surface temperat ure is probably 12°C or slightly below; temperature recording stations within 70 km on opposite sides from the cave have MASTs of 12.4° and 13.4°C, but the cave is at a higher elevation than either station. This cave is a good example of how knowledge of c ave temperature variation can lead to prediction of undiscovered sections. Our observations of a seasonally reversing air flow (into the known entrance in winter and out of it in summer) strongly point toward the existence of a second, previously unsuspect ed entrance. Furthermore, the direction of flow requires that the second entrance be higher in elevation than the one known, making this cave an example of Type 7, Figure 1. The tell tale air flow is quite strong in the stream passage beyond point E, indic ating that this passage leads toward the undiscovered entrance. Further evidence of a second entrance can be seen in the relative fluctuations of air and


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 25 wall temperature in the cave, to be discussed later. Given postulation of this second entrance, the p attern of temperatures observed within the cave are what would be expected. Location A shows the lowest January reading and the greatest January to August fluctuation, with B, H, and G following, in decreasing order. This follows the flow pattern of cool d ense air from the entrance, and the entire lower cave level is a cold air trap. It is not as cold as might be expected; cold air settles into this low area, but it is warmed by the stream which pools there before disappearing in a sump. Note the cooling ef fect of the lower cave on the stream, which enters the known cave (near E) at 12.0°C and progressively cools to 11.2°C at I. C is little affected by air from either entrance; it is too high relative to the known entrance to be cooled in winter, and too dis tant from the other to be greatly warmed in summer. Warm summer air being drawn into the upper entrance evidently has been cooled approximately to MAST by the time it reaches the known cave. D is an example of a relatively constant temperature room such as Z, cave type 7, Figure 1. Distance from the warm air (upper) entrance, plus small volume, prevent it from being a warm air trap. Temperatures at F are slightly lower than the presumed MAST, indicating that it is probably nearer to the known cooling entran ce than to the undiscovered upper one; its overall temperature stability, however, is indicative of its isolation from both entrances. The above two caves illustrate the impact of seasonally reversing air flow in multi entrance, multilevel caves. Cave num ber 6 of Figure 2 illustrates a more subtle example of seasonally reversing air flow. Its moderately large, sloping entrance, simple structure, and the distribution of volume both above and below entrance level allow year round air flow through the single entrance. When outside temperature rises above internal cave temperature, cool air spills out the bottom of the entrance. The "negative pressure" so created enhances movement of warm air through the upper part of the entrance into the upper sections of the cave. The size of the entrance is sufficient to allow the two opposing streams of air to pass simultaneously, and they are easily detected by an observer. In winter the relatively warmer cave air will rise through the entrance, being replaced by denser, c older air from outside (air flow arrows would reverse directions). In this type of cave, relative velocities of flow, summer versus winter, depend on the amount of volume above versus below the entrance. It is important to note that the two ends of the ca ve will have their major circulation at different times. The lower end will have greatest air flow in winter, and be a cold air trap in summer; the upper end will have greatest air flow in summer and act as a warm air trap in winter. Periods of temperature stability (deviating from MAST in opposite directions within the same cave) will be much longer and more predictable in this cave than in caves 1 or 2 of Figure 2. The range of temperatures between points C (below MAST) and D (well above MAST), and their relationship to MAST and the outside temperature illustrate the undulating passage creates a relatively stable MAST regime beyond F. On the day of observation there was no detectable air flow at B and C despite the rapid movement of air above. The outward moving flow of air along the ground outside (1.5 m below the point registering 26.7°) was 18.4°C. Non reversing Air Flow Cave number 3 of Figure 2 illustrates the impact of having all of the cave volume above entrance level. Its air flow pattern is like that of Type 5, Figure 1, although its elevational rise is only slight. The room containing C and D is a warm air trap, as demonstrated by an August temperature considerably in excess of MAST. Despite str ong winds which buffet the entrance from across a large reservoir, the large entrance size (2 m high by 11 m wide), the cave length of only 76 m, a direct, relatively unobstructed path from the entrance to the innermost volume, and its relatively small tot al volume, this cave does not become cold in winter; the warm air is trapped and very little flow occurs. Even at the end of a record cold winter in 1977, location D remained slightly above the local MAST. If there were a strong upward slope between points B and D and/or if the volume from C to D were greater in an upward direction, this cave's winter temperature would be even higher. Nevertheless, its annual average is well above that expected based on MAST. Some of the most remarkable thermal gradients k nown to structures similar to that illustrated in type 4 (Figure 1). A cave located in eastern Tennessee (see Figure 3), where the MAST is approximately 14°C illustrates this. Entrance A, just above the r im of a large sinkhole, slopes upward into the main chamber; entrance C, located 11 m below the rim in the bottom of the same sink, slopes down into


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 26 the cave. Entrance B, slightly below C, opens directly into the main chamber. In summer, cooled air from th e upper portion of the chamber spills out into the sink, which acts as a large dam. Consequently, on 18 July 1976, when the outside temperature at the rim of the sink (site 1) was 23.6°C, the temperature near the bottom of the sink (site 2), outside entran ce C, was 14.0°C (approximately MAST). A thermal range of 6.7 (site 3) to 23.5°C (site 4) existed in the main chamber (35 m tall, 54 m long and 12 to 20 m wide). A mild negative pressure created by the escape of cold air probably aids in drawing warm summe r air in through A and B; the temperature at the very top of the room may have been even warmer than that recorded at site 4. Though slight air flow is possible in summer, the cave's only strong air flow is limited to periods of cold winter weather. Multip le entrances and its greater overall volume above the highest entrance and below the lowest one, allows this cave to function as a more efficient cold and warm air trap than cave 6, Figure 2. Data from a second cave of very similar structure illustrate an annual temperature cycle in such a cave (Figure 4). Again, there is an elevational increase (roughly 35 m) from the bottom of the cave's main, large room to the cave's upper entrance. In this cave the main entrance room is 46 m long, 18 m wide and 15 m hi gh, with several major passages extending out to the sides and downward. A single large canyon passage approximately 25 m tall and 1.5 2 m wide connects the lower cave to an upper room that is approximately 27 m long, 18 m wide and 4 m high. The upper room exits to the surface at a level about 1 m below its upper end through an entrance less than 1 m in diameter. The larger lower room is entered through either of two entrances near the upper end of its ceiling, both of which average about 1 m wide by 2 in. high. Though this cave is more complex than the last, it serves as another good example of the fourth type shown in Figure 1. The record of air temperature from location A (Figure 4) in this cave is from a deep, inner room, protected from air flow by a ve ry narrow irregular passage and several vertical turns that act as ideal dams (as in Figure 1, example 2) against flow of either warm or cool air. As expected, air temperature there closely approximates MAST and shows an annual fluctuation of only 1.1°C. E ven this small fluctuation is thought to have been caused by the occasional use of the room as a roosting place for several thousand bats. Location B was in a major side passage roughly half way between upper and lower levels of the cave. Here air temperat ure varied by only 0.6°C, despite relatively free circulation of air, but constantly was below MAST. Site C was located in the uppermost room 18 m from the upper entrance. At this location small amounts of cold air "leaked' in, lowering temperatures in win ter, while slight summer loss of cool air from the lower entrances created sufficient negative pressure to draw warm outside air down into the room, resulting in a nearly 12°C annual fluctuation. The temperature record for site D, located near the bottom o f the main, lower room, 40 m from the lower entrances, shows an annual fluctuation of 5°C with the annual high temperature still 7.3°C below that expected based on MAST. Its large volume below the lowest entrance makes this main room an exceptionally effic ient cold trap. As in the previous example, the lower entrances were surrounded by a deep sinkhole which reduced loss of cold air. Summer air movement was slow enough that it was detected only at the small upper entrance. During cold winter weather a stron g flow of cold air enters the lower entrances, while relatively warm air exits through the single upper entrance. Air Flow Prevention As previously discussed, lack of elevational differences between multiple entrances, small entrance size (particularly in single entrance caves), and natural dams can reduce or nearly eliminate air circulation. When these characteristics are present, singly or in combination, the result generally will be caves or sections of caves with the relatively constant temperatures of popular legend. Cave 5 (Figure 2) provides a very simple example of the impact of a small entrance. The entrance passage into this cave includes a 5 meter long horizontal section that is only 1/4 m in height and 1.5 m wide. With an enlarged entrance, thi s cave would be of type 1 (Figure 1) and would fall well below MAST in winter, yet due to its restrictive entrance size and shape, its average air temperature on 6 February 1976 was less than a degree below MAST. The 18.8°C temperature near the lowest poin t in the cave may have reflected the impact of cold surface water flowing into the sinkhole entrance during winter rains. A prominent factor in reducing air exchange with the outside in this cave is the cross sectional shape of the entry passage. If the pa ssage were simply turned 90°, placing its greatest width in a vertical plane, this cave's annual temperature fluctuation likely would increase considerably. Warm and cool air could then exit and enter simultaneously.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 27 Figure 3. Cross section of an eastern Tennessee cave which acts as both a cold and warm air trap. Air circulation is greatest in winter. Surface Wind Cave 4 (Figure 2) of this study illustrates the relative ineffectiveness of surface wind, even on a tunnel like cave only 17 m long with two entrances (4.9 m wide by 1.4 m high and 3.5 m wide by 0.8 m high). Although a 15 KPH surface wind was blowing in the same direction as the c ave passage, the air temperature in this cave at 1700 on 6 February 1976 was more than 7° below the outside temperature and approximately 5°C below MAST. Despite this cave's small size, simple shape, relatively large entrances, and its directional orientat ion, the surface wind had only moderate impact; slight directional air flow along the cave ceiling in the expected direction was noted, and the 3° difference between air and wall temperature demonstrated that a relatively rapid rise in air temperature had occurred during the day. This cave and cave 3 (Figure 2) demonstrate that surface winds probably have little effect on any but the smallest and simplest caves. EFFECT OF WATER ON CAVE TEMPERATURE A central Tennessee cave with a single vertical entrance (6 m deep and 4 m in diameter; located in the bottom of a shaded, 8 m deep sinkhole) provides an excellent example of the potential impact of surface water on cave temperature. A 100 m section of passage below the entrance averages 11 m wide and 3 m tall and would be expected to have an average air temperature below the mean annual surface temperature of 14°C. Even if air circulation were poor, a cave below such a single sinkhole entrance should not exceed MAST. However, on 30 July 1976 we found that the air temperature 90 m inside the described large passage was 21.1°C, some 7°C above MAST. This could be accounted for only by the presence of a large stream flowing through the main passage below the cave entrance. Though the stream clearly fluctuates in size, at the time of our visit it averaged 7 m wide, 0.25 m deep, and was flowing rapidly. At its point of entry, the water temperature was 21.3°C (0.2°C warmer than the air 2 m above), but 90 m downstream it already had lost 0.1°C to the surrounding cave. Cav e air at that point (nearly directly below the entrance) was 20.3°C. Approximately 100 m farther downstream the air temperature was 19.4°C. At this point an upper level passage, averaging about 2 m in diameter slopes very slightly upward and continues for at least 100 m, and probably much farther. Air temperatures near the ceiling 25 and 75 m into this side passage were 17.2° and 15.3°C, respectively. At 95 m, just past the first downward dip in the passage, the air temperature near the floor was 14.3°C, ap proximating the expected temperature based on MAST. Clearly, the high temperature of this cave's stream had measurable impact on the cave's air temperature, even at a considerable distance beyond the main stream passage. Due to the structure of the cave's single entrance, it is very unlikely that warm air entered from outside. While working in caves of northwest Florida in winter, we repeatedly observed not only the impact of cold surface water, but also that of deep pools of subterranean water. Two caves less than 5 km apart illustrate these temperature differences. On 3 February 1976 the first cave was approximately half full of surface water from winter rains, and the water temperature was 11.4°C. Air temperature 1.5 m above the water ranged from 11.3° t o 12.4°C. The second cave, visited 5 February 1976, sloped sharply downward from its 2 m entrance and had an easily detected flow of cold air along its floor, with warm air exiting along the ceiling. Despite these characteristics (which favored entrapment and storage of cold air) its air temperature 28 m inside and 1.5 m above a pool of water roughly 30 m long, 12 m wide and more than 12 m deep ranged from 16.6° to 17.8°C. The water was of subterranean origin, and its temperature was 19.9°C, only 0.1°C abov e the MAST reported by a nearby weather station. RELATIONSHIP BETWEEN AIR AND WALL TEMPERATURE Wherever air in a cave is isolated from the external atmosphere it should come into thermal equilibrium with surrounding cave walls. As already noted, the locat ions of


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 28 Figure 4. Air temperatures (maxiumum/minimum, number of degrees in the range) at four sites in a northeastern Tennessee cave on 18 November 1975, and 13 January, 9 March, 1 August and 20 December 1976. The cave is similar to Type 4, Fig. 1, with the addition of a warm air trap near entrance B. MAST = mean annual surface temperature. such protected places are highly predictable, as are the locations of probable large differentials between air and wall temperatures. The magnitude of difference in air and wall temperature provides a test of one's assumptions regarding constancy o f temperature for any given location: areas of assumed constant temperature should show consistent equilibrium of air and wall temperatures. (It should be remembered, however, that even areas of great fluctuation may frequently exhibit air/wall temperature equilibrium, for example, during sustained periods of minimal air flow.) Air/wall temperature differences should be greatest near cave entrances where air enters. Near average above wall temperature in summ er, while it should average below wall temperature in winter. However, these expected differences will decrease with distance of air flow through a cave, so that even rapidly moving air exiting through distant entrances may have reached equilibrium with su rrounding walls. Accordingly, analysis of air/wall temperature differences (Figure 5) in cave 2 of Figure 2 provided additional evidence in favor of the existence of a second, unknown entrance, as noted previously. Near the known entrance (site A), which differences between air and wall temperatures occurred in November and January (air temperature below wall temperature). Differences were very small in March, May, and August (with air slightly higher than wall in tempe rature, and both still below MAST), when the near the end of the known cave, on the way to the undiscovered entrance; the greatest difference occurred in May (air higher than wall temperature), and the least in during the spring on its way from the undiscovered to the known entrance. The relative slowness of wall temperature response to air temperature fluctuations is pointed out by the August Novem ber and January March readings at sites A and F where air temperature drops below wall temperature with the beginning of cold weather, and rises above wall temperature in spring. Finally, site C, which is relatively isolated from either entrance and from a ir flow (as noted previously), exhibits the expected minimal air/wan temperature difference. When comparing differences in air and wall temperatures it is important to remember that, regardless of season, both the amount and direction of air flow will be determined by the amount and direction of differences between inside and outside temperature. These differences may fluctuate widely, not only as a result of the passage of storm fronts, but also on a daily basis, due to night day changes. Although we visi ted the respective locations of temperature measurement in cave 2 at approximately the same time of day each visit (to maximize comparability of readings among visits), we recorded several day to day and within day fluctuations between air and wall tempera tures at location A in order to illustrate the potential extent of such fluctuations. On 28 December 1976 the air temperature in front of the known entrance was +8.6°C at 1145 hr and 2.8°C at 2250. At 1200 the air temperature at location A was fluctuatin g from 5.8 to 6.1°C, and the wall temperature was 3.9°C. (Unfortunately no temperatures were recorded at location A at 2250.) Clearly, outside temperatures during the previous night had fallen well below freezing, and the cave walls, cooled by that incomin g night air, were now being warmed but were still cooling incoming air to below the higher daytime temperature.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 29 Figure 5. Air a nd wall temperatures through a seasonal cycle at 3 sites in cave number 2, Fig. 2. Dates of the measurements are 15 November 1975, and 10 January, 6 March, 16 May and 18 August 1976. The reverse situation is well illustrated by data from the following exceptionally cold day. At 1250 on 29 December 1976 the outside temperatur e was 6.1°C, and at 1935 the temperature had fallen to 8.2°C. Inside the cave at 1300 the air temperature at location A was fluctuating from 3.3 to 2.9°C, and the wall temperature was 0.8°C. At 1925 the air temperature at this site had continued to fal l, varying from 4.7 to 4.5°C, and the wall temperature was 1.4°C. On this day continually falling outside temperature prevented the situation recorded on the previous day when inflowing air was warming the cave walls. On the second day incoming air rang ed 2.1 to 3.3°C lower than wall temperature, as opposed to 1.9 to 2.2°C above wall temperature on the previous day. The first average daily cycles. These data probably can explain the contradiction between our findings and those of several previous authors who claimed that wall temperatures in caves are normally about 1 C lower than that of adjacent air masses (Twente, 1955; Nieuwenhoven, 1956, Hall, 1962; McNab, 1974). These researchers limited their inves tigations to winter studies of hibernating bats. Bats normally hibernate in caves whose structures act as cold air traps, and such caves tend to take in more and colder outside air at night than during the warmer days. By mid or late morning, when researc hers generally arrive at their caves, air flow often has slowed considerably and may have stopped altogether. Nevertheless, the last air drawn in was probably considerably warmer than the coldest night air, leading to the observation that air temperatures are generally higher than those of adjacent walls. RELATIONSHIP BETWEEN AIR MOVEMENT, TEMPERATURE, AND HUMIDITY A thorough study of cave humidity and the subtle interrelationships between humidity and the many factors that may bear upon it is far beyond t he scope of our research. We did, however, make sporadic comparisons among humidity, temperature, and air movement in 10 of the caves investigated. Substrate type, ground moisture, and the presence of streams or standing water all contribute to basic cave humidity levels. Superimposed upon these basic factors, rates of humidity and temperature of air entering from outside compared to existing cave conditions were found to be of importance in determining dai ly and seasonal patterns of humidity. Regardless of season or temperature of the inflowing air, relative humidity was lowest near the entrance where outside air entered. A gradient of increasing relative humidity existed between the places of entry and exi t of the flow. Further, in caves with seasonally reversing air flow, passages that have low relative humidity at one season may have high relative humidity at another. These patterns are illustrated by our recordings from cave 2 (Figure 2). On 10 January 1 976 when air movement was past locations A, B, H, G, and E, in that order, sample relative humidities were as follows: B -49 percent; halfway between H and G -82 percent; halfway between G and E -86 percent; halfway between E and D (upper cave: air f low nearly nonexistent) 98 percent. The movement of outside air through the cave clearly affected relative humidity levels along its route. On 16 May, when the direction of air flow had reversed (passing from E to D, C, B, and A), the relative humidity hal fway between E and D had dropped as expected (to 88 percent). No other measurements were taken on that visit. Strong air flow has been considered by some to be closely


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 30 associated with low humidity throughout a cave (Vandel, 1965; Barr, 1968). Although it is true that air flow often can be a desiccating influence, particularly near "sucking" entrances in winter, ground moisture or areas of water can increase relative humidity of even strongly flowing air to near saturation as it passes through the cave. For example, despite the fact that troglobitic trechine beetles are limited to areas where the relative humidity is 98 percent or above (Barr, 1959), a number of individuals of three species have been observed feeding in a "wind tunnel" in a Kentucky cave whe re the air flow exceeded 40 m per minute (Barr, 1968). Barr seemed puzzled by this apparent contradiction, but we suspect that the contradiction was only apparent -as we have pointed out, rapidly moving air in caves is not necessarily dry. One of us (Tutt le) once made a similar observation of trechine beetles in a "wind tunnel" in a Kentucky cave; the relative humidity was 98 percent, despite the strong air flow. In reference to the relationship between the total volume of air flow through a cave system a nd the cave's humidity, it also is important to note that air flow rates will vary greatly in different sections of the cave even along the main route of flow. For example, in a single passage, diameter and shape may vary dramatically, so that a given volu me of air flow through the area would be rapid and potentially very influential on humidity in a narrow section while remaining virtually undetectable in a very large area. Within the parameters discussed in this section, however, our limited data indicate that overall patterns and timing of relative humidity changes are largely correlated with, and dependent upon, predictable daily and seasonal patterns of air flow. Finally, although it is usually relative humidity which is reported in the literature, it is important for cave biologists to keep in mind the distinction between this measurement and absolute humidity (mass of water vapor present in a unit volume of atmosphere). In some instances the two measurements follow the same relationship from site to s ite. This is the case for the cave 2 example above -absolute humidities (in the same site order, in g/m 3 ) on 10 January were 2.6, 7.5, 8.0 and 9.9. The 16 May absolute humidity had dropped to 8.8. In other cases, high relative humidities at low temperature s actually may be more potentially dessicating than lower relative humidities at higher temperatures, due to the lesser amount of water vapor present in the air in the former case. For example, in the cave discussed in Figure 4 the relative humidity at loc ation C on 10 January 1976 was 99 percent. On 1 August 1976 it was only 92 percent. Although the August relative humidity was lower, absolute humidity was nearly two times higher -15.5 g/m 3 in August versus 8.4 g/m 3 in January. In a similar cave (Figure 3) the relative humidity on 18 July 1976 was only 70 percent in the path of incoming air (site 4), while it was 100 percent at the floor of the same room (site 3) and 99 percent just inside entrance C (where air exited very slowly). These relative humidities follow the pattern discussed in the paragraph above but, due to the great temperature gradient in the room, absolute humidities (14.1, 7.6 and 8.8 g/m 3 respectively) are totally reversed in relationship among sites. Temperature of the air, due to its effe ct on absolute humidity, must be included in the list of factors considered in evaluating the impact of a cave's humidity regime on its faunas. BIOLOGICAL IMPLICATIONS Humidity is a very important environmental parameter for many terrestrial cavernicolous animals (Barr, 1959, 1961, 1967; Vandel, 1965). Cold dry air entering a cave in winter, as it warms inside, certainly can be a dessicating influence to organisms in that area. In particular, respiratory water loss for an animal with a body temperature war mer than the air will be more severe the greater the temperature difference. It is important to note, however, that besides the large scale factors influencing humidity (discussed in the previous section), a number of other considerations influence the eff ect of given levels of air flow and humidity on organisms. The size of the boundary layer associated with a particular organism's coupling with its environment is proportional to the size of the organism and the roughness of the substrate on which the anim al rests, as well as to the wind speed (see Juberthie, 1969, for a cave study of microclimate). Substrate moisture in many situations, then, may be of more importance to small arthropods than air moisture. In other words, in addition to the fact that flowi ng air in a cave is not always dry, different organisms in a particular area of cave in fact may be exposed to very different environments -low air humidity (relative or absolute) may have little effect on a small terrestrial arthropod on a rough, moist fl oor compared with its effect on a bat. Air flow, despite its potential for lowering humidity, should not be assumed to be entirely bad for most or even any cave organisms. It may be of considerable importance as a directional cue for some cave animals. Tr echine beetles are reported to be highly sensitive to air flow (see Barr, 1968), and two species of cave crickets


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 31 (Ceuthophilus conicaudus and Hadenoecus subterraneus) are believed to use air currents in their orientation to and from cave entrances (Reichl e et al., 1965; Campbell. 1976; Levy, 1976). Additionally, air flow and associated patterns of temperature and humidity are as predictable in many caves as are many other cues that are used by surface animals. Many cavernicolous animals are thought to be e xtremely sensitive to even slight changes in air flow, temperature, and humidity (Barr, 1959, 1961, 1964, 1967; Vandel, 1965), and the role of air flow as a seasonal or daily cue may be of major importance in some caves. Beyond the cue effects of air move ment and temperature, temperature directly affects a variety of trogloxenes (animals that live in caves but cannot complete their life cycles without leaving caves). Bats will be discussed in detail later. Our casual observations indicate that cold caves w hich harbor hibernating bats often additionally serve as hibernating sites for a variety of otherwise surface arthropods (e.g. culicine mosquitoes and the noctuid moth Scoliopteryx libatrix) that were not often found in warmer caves. On the other hand, the se same cold caves rarely contained amphibians, such as Eurycea lucifuga and Plethodon glutinosus (even when relative humidity remained high), which often were abundant in other caves nearby. Even if the major effects of air movement and temperature were l imited to determining the within and among cave distributions of such trogloxenes as bats and cave crickets, they ultimately could exert strong indirect effects on troglobitic (animals that are so highly specialized that they cannot live outside of caves) and troglophilic (animal that often live their entire lives underground but also can live in moist places under rocks or logs on the surface) cave animals that depend on these animals as primary sources of energy. Dependable food sources in a cave environ ment are of vital consequence to its fauna; whether they be guano from bats and crickets, entrance litter, or detritus from floods, supplies vary seasonally (Barr, 1967). Strong selective pressure must exist for the development of responses to such availab le cues as changes in water temperature, pH and oxygenation (for aquatic animals), air flow, temperature and humidity (for terrestrial animals), and flooding. In fact, initial studies indicate that many troglobites, both terrestrial and aquatic, use season al flooding to time peaks of reproduction (see Barr, 1968; Poulson and Smith, 1969; Juberthie, 1975, among others). Clearly, the potential impact of the above environmental factors in determining species survival and distribution is great and the problems complex. We make no pretense of understanding more than the potential importance of these variables. It is important, however, to note the extent to which the environment of the cave depends on its exchange of air and water with the outside. Hopefully, ou r discussion of cave structure and the causes and predictability of daily and seasonal patterns of air flow, temperature, and humidity will act as a stimulus for much further investigation of these potentially important environmental parameters. Temperatu re Constraints on Cave Bats For most bats, and especially for cave dwelling species, the selection of appropriate roosting temperatures is of critical importance (Harmata, 1973). Twente (1955) noted that it was vital for bats to choose roosts with temperat ures appropriate to the desired metabolic processes: warm for digestion and growth in the summer, and cool for torpor in the fall and winter, with the exact optimum temperatures varying somewhat among species. McManus (1974) found that hibernating Myotis l ucifugus in a New Jersey mine "demonstrated a clear preference for temperatures near 2°C the temperature at which Hock (1951) found the species' oxygen consumption to be lowest. Harmata (1969) demonstrated that Rhinolophus hipposideros could select "the pr oper temperature of hibernation" with accuracy as near as 0.8°C. Whatever the mechanism of selection, microspatial distribution preferences and movements along temperature gradients also have been demonstrated in summer roosts of many species, with cluste ring playing a role in behavioral temperature regulation then as well as in winter (Licht and Leitner, 1967; Harmata, 1969, 1973; Tuttle, 1975; Trune and Slobodchikoff, 1976, among others). A number of authors have noted the high metabolic cost of the wron g ambient temperature for bats (Hock, 1951; Herreid, 1963; Stones, 1965; Davis, 1970; McManus, 1974). For cave dwelling species, caves with roosts of appropriate temperatures are limited in number. At extremely high latitudes caves may be too cold for use at any time. At somewhat lower latitudes, where MAST ranges 2 to 12°C, caves often provide appropriate hibernating quarters but are normally too cold to permit summer use. In areas of intermediate latitudes (MAST 12 to 20°C most caves are too warm in wint er and too cold in


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 32 summer, and few are used by bats in any season. At lower latitudes nearer the equator, increasingly warm caves are ideal for maternity use but unsuitable for hibernation (Dwyer, 1971). Throughout most of the cavernous areas of the Unite d States, caves are of the intermediate type with regard to temperature. Consequently, although bats may be able to utilize them in spring or fall when their temperatures may be acceptable (Harmata, 1973), most U.S. caves are unsuitable for bat use for sum mer nurseries or winter hibernacula. Thus, those species that use caves are often severely roost limited. (The problem is compounded for species which use caves in summer, since the cave must have not only appropriate temperatures available but also must b e close enough to proper feeding habitat.) Distribution of caves of appropriate temperature, then, likely plays an important role in the determination of many distributional boundaries (McNab, 1974; Humphrey, 1975). For example, although numerous caves an d mines exist in Utah, Twente (1960) concluded that virtually all were of inappropriate structure to provide temperature ranges essential to bat hibernation. He did not find a single suitable cave or mine among more than 500 examined. Additionally, the end angered gray bat ( Myotis grisescens), a species which uses caves year round, appears to be limited in its north south distribution primarily by the absence of warm caves for rearing young in the north and by a lack of cold hibernating sites in southern cav es (Tuttle, 1975, 1976). Few caves anywhere within its range provide roosts of appropriate temperature, and even in Alabama, where gray bats probably were once most abundant, this species is not known to have ever occupied more than 2.4 percent of the area 's 1635 known caves in summer or 0.1 percent in winter (Tuttle, in press). This is despite the fact that this species is behaviorally able to reduce thermoregulatory costs during summer by clustering together in large numbers in ceiling domes or in restric ted passages where heat can be trapped (Tuttle, 1975), thereby utilizing otherwise marginal caves. Since most U.S. caves are in the intermediate, unusable range of temperature, cave bats generally are forced to select the very few caves that have structure s permitting them to deviate well above MAST (for summer use) or below (for winter use). Structures of caves chosen for winter hibernation are easily predictable. Except at high latitudes or elevations, they almost invariably fall into categories 1, 4, 6 o r 7 (Figure 1). Of these, Type 4 is by far the best. Without a cold air trap, Type 6 does not provide adequate stability. A midwinter period of outside warmth could prove highly detrimental to bats (many of which cannot go out to feed) hibernating in a sim ple cave of this type. A small, simple cave of Type 1 could prove equally unsatisfactory in an unusually cold winter. Accordingly, among the eight largest bat hibernating caves known in the Southeast, five are of Type 4 and three are Type 7. All of these o ccupied caves are large and have structural complexity adequate to provide temperatures ranging from near freezing to 12 to 15°C. Summer maternity roosts usually are restricted to heat traps, especially in caves of Type 6 (if a trap exists) and 5 and 7 (w best). Myotis grisescens, despite its ability to heat summer roosts by aggregating in large colonies, still prefers caves of these types; one of the largest maternity colonies ever known existed in Cave 3 (Figure 2), a Type 5 cave. Although few observations of summer cave colonies of Plecotus rafinesquii have been made, the several maternity colonies observed by us in southeastern caves each numbered fewer than 200 individuals. Such small colonies lack the ability to heat roosts of marginally low temperature, and as might have been expected, each was located in a heat trap of the kind illustrated by Xs in Types 5 and 7 (Figure 1). Temperatures in these roosts were all between 21° and 25°C, although MAST ranged only 14° to 16°C. Other examples could be presented, but it is sufficient to point out that bats must either abandon caves during the maternity period, seek exceptionally efficient heat traps near cave entrances, or heat their cave roosts by clustering togethe r in very large numbers on domed ceilings (a strategy for which any benefit must be balanced against the cost of increased intraspecific competition for food). Successful growth and survival of young gray bats depend on the success of one of the last two s trategies (Tuttle, 1975). Finally, the ideal bat cave is generally one which offers a large thermal range. Ability to move among temperature zones within a cave can allow bats to control embryonic development (thereby synchronizing parturition time -Racey , 1969; Dwyer and Harris, 1972), to achieve deeper torpor when stressed by inclement weather during summer or when fat acquisition becomes important in late summer, or to adjust to temperature fluctuations throughout a season or between years. Obviously, s tructural and elevational complexity and increased cave size generally will contribute to this desired thermal range. Tall canyon


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 33 passages often provide especially suitable temperature gradients for winter hibernation. It is rare for any one cave to provi de sufficient thermal complexity for year round occupation; seasonal migration between caves is usually necessary for bats which use caves year round (see Tuttle, 1976). Two caves discussed in this paper, however, are important to bats both in winter and s ummer. The cave (discussed in the section on Nonreversing Air Flow) from which the readings in Figure 4 were taken houses one of the largest winter populations of Myotis grisescens known, as well as a sizeable summer bachelor colony of the species. The hib ernation roosts are in areas of the cave which are protected from freezing but are well ventilated by cool winter air; the summer roosts are in warm areas much higher in the cave. The second such cave, Cave 1 of Figure 2, contains the largest summer colon y of Myotis grisescens known. The main roost, located in the dome like area around H, is warmed by the summer air sucked in from entrance K by the strong air circulation discussed previously, and by the body heat of the colony of 128,000 bats (formerly mor e than 250,000). In winter, the appendix like area (F), due to its configuration and location, traps and stores air of low temperature, providing a hibernation roost of relatively constant temperature for a number of bat species, including M. grisescens an d M. sodalis . MANAGEMENT IMPLICATIONS Choosing Caves for Protection Clearly, knowledge of cave structure and its relation to temperature and humidity is of potentially great importance in predicting species distributions within and among caves, and in det ermining the relative merits of any given cave for protection. Data on such factors as number, size, shape and location of entrances, internal passage size, contour and slope, distribution and amount of volume relative to cave entrances, and source and amo unt of water flow (if any), can be used to predict and/or verify the probable seasonal temperature and humidity regime of a cave. Given the limitations of resources, time and manpower, it often is important to establish criteria for recognition of caves of special or unique merit. Obviously no single structural type can be singled out for exclusive protection, since each cave type presents a potentially different setting for the evolution of different faunas and survival strategies. In fact, a wide variety of cave types should be protected. For example, caves that are good for bat hibernation may not be good for some terrestrial cavernicoles, and vice versa. Frequently the object of cave protection is centered around one or two endangered species. In such si tuations it is vital to ascertain not only the species' temperature, humidity, and other microhabitat requirements, but also its food requirements and sources when relevant, in order to guarantee that all important parameters are adequate. For bats, when food supply availability and other external variables are equal, caves of greatest structural and therefore thermal complexity generally are best. Nevertheless, in the case of maternity colonies, where warmth is of primary concern, even simple caves (for e xample cave 3, Figure 2) may be of great importance. Also, in the case of endangered bats, their present usage of a cave often is not a reliable indicator of its suitability for use. The best caves often have been heavily disturbed and now contain very few bats. On the other hand, other nearby caves, of very marginally suitable temperature but less disturbed, may contain more bats. In many cases the most important cave, in terms of the species' longterm survival, is the one that presently has few bats. A g ood example is illustrated in Figure 3. As a result of this cave's popularity with local cavers, it has not housed major bat populations for perhaps as long as 50 or more years. Although no bats were present at the time of our visit, scattered recent dropp ings indicated that some bats continue to visit the cold area at night in the summer and probably in the fall. If the cave were protected, it could potentially become an important bat hibernating site, as it undoubtedly once was prior to disturbance. In ad dition to its cold trap characteristics, which make it suitable for hibernation, there is evidence (in the form of feces) in the warmest area, which indicates that some bats continue to attempt to use the area as a summer roost. Similarities with known roo sts suggest that the species involved may be Plecotus rafinesquii. In this case as in many others, then, the cave's structure and resulting environment can tell more about its importance to bat populations than does its present degree of usage. This is alm ost certain to be true for caves valuable to other animals as well. Means of Protecting Caves Knowledge of factors affecting cave environments also is of great importance in determining the proper means of cave protection. In a number of instances, improp er gating of caves has reduced or destroyed the bat populations intended for protection, either through reducing free access by the bats or reducing the air flow necessary for


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 34 maintenance of appropriate temperature and humidity (Mohr, 1972; Tuttle, 1977). Creation of additional entrances also can have disastrous results. Specific recommendations for cave protection through gating or fencing are provided by Tuttle (1977). In brief, structures which in any way alter air flow should be avoided. Any structure w hich blocks an entrance can affect not only air flow, but also the supply of food (in the form of entrance debris) for those cavernicoles requiring within cave sources. In general, it is sound policy to simply avoid tampering directly with an entrance unle ss absolutely necessary. It is of interest to note that alterations in temperature and humidity can have negative effects not only on cave life, but also on cave formations by altering development. Furthermore, protection or destruction of one species may influence the survival of a whole group of other species; for example, protection of a summer bat colony protects the whole guano ecosystem which may be present. Another vital factor for the public and individuals responsible for caves to be aware of is t hat even actions outside of caves can have great impact inside; in particular, smoke from fires built in or near an entrance can be drawn into a cave, as McCavit (1975) noted. At the very least, unnecessary disturbance is the result; at the worst, whole po pulations of bats and perhaps other animals may be killed. Hopefully, this discussion of the factors influencing cave environments and our examples will prove useful to those who deal with caves in a scientific, managerial, or recreational capacity. It is apparent that, at times, lack of understanding of the many complexities involved has impeded the progress of both research and protection of faunas. Improved understanding of these factors, combined with increased knowledge of cavernicolous species habita t requirements, should provide guidelines for utilization and/or protection of valuable cave resources. ACKNOWLEDGEMENTS Thomas Poulson critically read an early draft of this manuscript and provided many helpful suggestions, and Richard Wallace assisted u s in the field. Ralph Jordan, Rick Morgan and John Thurman of the Division of Forestry, Fisheries, and Wildlife Development, Tennessee Valley Authority, provided much logistical and personal assistance, and our field work was supported contractually by the Tennessee Valley Authority. LITERATURE CITED Barr, T.C. 1959. New cave beetles (Carabidae, Trechini) from Tennessee and Kentucky. J. Tenn. Acad. Sci. 34:5 30. -1961. Caves of Tennessee . State of Tenn. Dept. Conservation and Commerce, Div. Geol., Bull ., 6 4, pp. 1 567. -1964. Cave ecology. Science, 144021322. -1967. Observations on the ecology of caves. Amer. Natur., 101 475 492. -1968. Cave ecology and the evolution of troglobites. Pp. 35 102 in Evolutionary Biology, Vol. 2 (T. Dobzhansky, M.K. Hecht and W.C. Steere, eds.), Appleton Century Crofts Publ., New York. Campbell, G.D. 1976. Activity rhythm in the cave cricket, Ceuthophilus conicaudus Hubbell. Amer. Midl. Nat., 96:350 366. Conn, H.W. 1966. Barometric wind in Wind and Jewel Caves, South Dakot a. Bull. Nat. Speleo. Soc., 28:55 69. Cropley, J.B. 1965. Influence of surface conditions in large cave systems. Bull. Nat. Speleo. Soc., 27:1 10. Daan, S., and H.J. Wichers. 1968. Habitat selection of bats hibernating in a limestone cave. Zeit. Saugetierk ., 33: 262 287. Davis, W.H. 1970. Hibernation: ecology and physiological ecology. Pp. 265 300 in Biology of Bats, Vol. I (W.A. Wimsatt, ed.), Academic Press, New York. Delay, B. 1974. Les conditions thermiques des mileux terrestres dans la zone d'heterothe rmie des massifs calaires et leurs influences sur le developpement de Speonomus longicornis (Coleoptere, Bathysciinae). Ann. Speleol., 29: 121 36. Dwyer, P.D. 1971. Temperature regulation and cave dwelling in bats: an evolutionary perspective. Mammalia, 35 :424 453. -and J.A. Harris. 1972. Behavioral acclimatization to temperature by pregnant Miniopterus (Chiroptera). Physiol. Zool., 45:14 21. Eckler, A.R. 1965. An analysis of air fluctuations in two breathing caves. Pp. 105 113 in Speleo Digest 1963 (A.P . Haarr and W.C. McGrew, eds.), Pittsburgh Grotto Press, Nat. Speleo. Soc., Pittsburgh, Pa. Encyclopedia Britannica . 1975. 15th Edition, Encycl. Brit. Inc., Chicago, Vol. 1, p. 627. Geiger, R. 1965. The microclimate of caves. Pp. 462 467 in The Climate Nea r the Ground, Harvard Univ. Press, Cambridge, Mass. Hall, J.S. 1952. A life history and taxonomic study of the Indiana bat, Myotis sodalis. Reading Publ. Mus. and Art. Gallery, Sci. Publ . No. 12. Halliday, W.R. 1954. Ice caves of the United States. Pp. 3 2 8 in The American Caver, Bull. Nat. Speleo. Soc., No. 16. Harmata, W. 1969. The thermopreferendum of some species of bats (Chiroptera). Acta Theriologica, 14:49 62. -1973. The thermopreferendum of some species of bats (Chiroptera) in natural conditions. Z esz. Nauk. Uniw. Jag., Zool., Krakow, 19:127 141. Herreid, C.F., II. 1963. Temperature regulation and metabolism in Mexican freetail bats. Science, 142:1573 1574 Hock, R.J. 1951. The metabolic rates and body temperatures of bats. Biol. Bull., 101:289 299. Humphrey, S.R. 1975. Nursery roosts and community diversity of Nearctic bats. J. Mamm., 56:321 346. Jegla, T.C., and T.C. Poulson. 1970. Circannian rhythms I. Reproduction in the cave crayfish, Orconectes pellucidus inermis. Comp. Biochem. Physiol., 33:347 355. Juberthie, C. 1969. Relations entre le climat, le microclimat et les Aphaenops cerberus dans la Grotte de SainteCatherine (Ariege). Ann. Speleol., 24:75 104. -1975. Vie southerraine et reproduction. Bull. Soc. Zool. France, 100:177 201. -and B. Del ay. 1973. Influence des facteurs abiotiques, temperature et nature du substrat, sur le developpement embryonnaire du Coleoptere Bathysciinae trogobie Speonomus longicornis. Ann. Speleol., 4:689 696. Levy, E.S. 1976. Aspects of the biology of Hadenoecus sub terraneus with special reference to foraging behavior. M.S. Thesis, U. Ill. Chic. Circle, 219 pp. Licht, P., and P. Leitner. 1967. Behavioral responses to high temperatures in three species of California bats. J. Mamm., 48:52 61. McCavit, W. 1975. Bat popu lations. Michiana Caver, 2:62 64. McManus, J.J. 1974. Activity and thermal preference of the little brown bat, Myotis lucifugus, during hibernation. J. Mamm., 55:844 846. McNab, B.K. 1974. The behavior of temperate cave bats in a subtropical environment. E cology, 55:943 958.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 35 Mohr, C.E. 1972. The status of threatened species of cave dwelling bats. Bull. Nat. Speleo. Soc., 34:33 47. Moore, G.W., and B.G. Nicholas. 1964. Speleology, the study of caves. D.C. Heath, Boston, Mass., 120 pp. Nieuwenhover, P.J. van. 1956. Ecological observations in a hibernation quarter of cave dwelling bats in South Limburg. Publ. Natuurhist. Genoot. Limburg, 9:1 55. Peck, S.B. 1976. The effect of cave entrances on the distribution of cave inhabiting terrestrial arthropods. Int. J. Speleol., 8:309 321. Peters, W.H. 1965. Air density and temperature as a cause of the breathing phenomenon. Pp. 103 104 in Speleo Digest 1963 (A.P. Haarr and W.C. McGrew, eds.), Pittsburgh Grotto Press, Nat. Speleo. Soc., Pittsburgh, Pa. Plummer, W.T. 19 64. A note on cave breathing. Pp. 101 107 in Speleo Digest 1962 (A.P. Haarr and W.T. Plummer, eds.) Pittsburgh Grotto Press, Nat. Speleo. Soc., Pittsburgh. Pa. Porter, C. 1974. Air flow through cave entrances. Pp. 73 74 in Speleo Digest 1968 (J.0. Davi s, R.A. Smith, W.B. Sherborne, and L. Power, eds.) Speleo Press, Austin, Texas. Poulson, T.L. 1964 . Animals in aquatic environments: animals in caves. Pp. 749 771 in Handbook of Physiology (D.B. Dill, ed.), Amer. Physiol. Soc., Washington. -1975. Symposiu m of life histories of cave beetles: an introduction. Int. J. Speleol ., 7:1 5. -and M. Smith. 1969 . The basis for seasonal growth and reproduction in aquatic cave organisms. Proc . 4th Int. Cong. Speleol. , Lujbljana, Yugoslavia, Vol. 4 5: 197 201. -and W. B. White. Science , 165:971 981. Racey, P.A. 1969 . Diagnosis of pregnancy and experimental extension of gestation in the Pipistrelle bat, Pipistrellus subflavus . J. Reprod. Fert ., 19:465 474. Reichle, D.E., J.D. Palmer and 0. Park. 1965 . Persistent rhythmic locomotor activity in the cave cricket, Hadenoecus subterraneus, and its ecological significance. Amer. Midl. Nat ., 74:57 66. Russell, W.H. 1974 . Unusual types of cave air movements. Pp. 40 44 in Speleo Digest 1967 (G.D. McCutchen, ed.), Pittsburgh Grot to Press, Nat. Speleo. Soc., Pittsburgh, Pa. Schmidt, V. 1959 . The "ins" and "outs" of Breathing Cave. Nat. Speleo. Soc. News , 17:6 8. Stones, R.C. 1965 . Laboratory care of little brown bats at thermal neutrality. J. Mamm ., 46:681 682. Trune, D.R., and C.N . Slobodchikoff. 1976 . Social effects of roosting on the metabolism of the pallid bat ( Antrozous pallidus ). J. Mamm ., 57:656 663. Tuttle, M.D. 1975. Population ecology of the gray bat (Myotis grisescens): factors influencing early growth and development. O cc. Pap . Mus. Nat. Hist., Univ. Kans., 36:1 24 . -1976. Population ecology of the gray bat (Myotis grisescens): philopatry, timing and patterns of movement, weight loss during migration, and seasonal adaptive strategies. Occ. Pap . Mus. Nat. Hist., Univ. Ka ns., 54:1 38. -1969 . The cave environment. -1977. Gating as a means of protecting cavedwelling bats. Pp. 77 82 in Natl. Cave Management Sym pos. Proc. , 1976 (T. Aley and D. Rhodes, eds.), Speleobooks, Albuquerque, N.M. Tuttle, M.D. Status, causes of decli ne, and management of endangered gray bats. J. Wildlife Man., in press. Twente, J.W., Jr. 1955. Some aspects of habitat selection and other behavior of cavern dwelling bats. Ecology, 36: 706 732. -1960. Environmental problems involving the hibernation of bats in Utah. Proc. Utah Acad., 37:67 71. U.S. Department of Commerce. 1975a. Climatological data, Alabama. Annual summary. U.S. Dep. Commer. Publ, Vol. 81. -1975b. Climatological data, Kentucky. Annual summary. U.S. Dep. Commer. Publ., Vol. 70. -1975c. Climatological data, Tennessee. Annual summary. U.S. Dep. Commer. Publ., Vol. 80. Vandel, A. 1965. Biospeleology: The Biology of Cavernicolous Animals. Pergamon Press, Oxford, 524 pp. Wilson, J. 1975. The effect of low humidity on the distribution of Heter omurus nitidus (Collembola) in Radford Cave, Devon. Trans. Brit. Cave Res. Assoc., 2:123 126.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 36 Guidelines for the Protection of Bat Roosts J. Mamm ., 73(3):707 710, 1992. The American Society of Mammalogists recognizes the need for g uidelines to regulate activities in and around bat roosts. In developing these guidelines, the Conservation of Land Mammals Committee has weighed the need for protection from disturbance against the needs for legitimate scientific inquiry and or monitoring declining bat populations. These guidelines are intended to assist field biologists and state and federal agencies charged with the granting of toward high professional standards and its opposition to a ctivities that could endanger bat colonies. The preservation and conservation of bat roosts, especially caves, is probably the most important issue in bat conservation, particularly since many roosts are traditional and used by successive generations of b ats over many years (Hill and Smith, 1984). One of the most important factors in the decline of bat populations in the United States and around the world is the destruction of roost sites. Roost sites (caves) are a limited resource that seasonally contain a high proportion of many species. Bats, particularly when concentrated in caves or other structures, are extremely vulnerable. Despite their generally small size, bats have low reproductive rates and long generation times and cannot sustain elevated rates of mortality or depressed levels of recruitment (Hill and Smith, 1984; McCracken, 1989). Of the 39 species of bats in North America north of Mexico, at least 18 species rely substantially on caves as roosting sites, and many of the remaining 21 species re ly on caves during some time of the year (Barbour and Davis, 1969; McCracken, 1989). The fact that large numbers of individuals often are concentrated into only a few specific roost sites results in high potential for disturbance. Cave dwelling bats are es pecially sensitive to both direct disturbances, such as human entry, and indirect disturbances to the roost and surrounding habitat. Persons entering maternity colonies can cause bats to abandon young or drop them to the floor from where they are usually n ot retrieved and subsequently die (Gillette and Kimbrough, 1970; McCracken, 1989). In addition, the handling of pregnant females has been known to cause abortion (Gunier, 1971). Disturbance during hibernation may cause bats to arouse prematurely, elevatin g their body temperatures and utilizing stored energy reserves, which usually cannot be spared. Bat specialists have estimated that each arousal of hibernating bats can rob them of 10 to 30 days of stored fat reserves (Thomas et al., 1990; Tuttle, 1991). B ats may return to a state of torpor after disturbance, but then may not have sufficient energy to survive the rest of the winter. In addition, bat caves are vulnerable to habitat alteration and degradation. Changes in cave microclimate (e.g., humidity, tem perature and air flow) are imposed through modification of cave entrances. Clearing trees from around cave entrances may result in an overall increase in summer temperatures or a decrease in winter temperatures, both of which may render a cave uninhabitabl e. The natural air flow in and out of a cave or its humidity may be altered to such an extent that the habitable portions are reduced or eliminated (Hill and Smith, 1984). Disturbance and destruction of roosts, especially caves, have contributed to the lis ting of many species and subspecies of bats on the U.S. Fish and species (McCracken, 1989; Mohr, 1972). Such designations and the subsequent recovery efforts require bat specialists and wildlife managers to monitor remaining populations. Guidelines presented herein should be considered as minimum precautions when dealing with roosts containing endangered or threatened taxa. These guidelines should also be considered when working with other bat roosts as w ell, because severe reduction or elimination of populations through careless entry may eventually lead to additional species and subspecies being threatened. In addition, we know very little regarding the actual status of some populations of most bat speci es, and many species that are not listed as threatened may warrant listing and need the protection that goes along with it (McCracken, 1989; Stebbings, 1980). Moreover, several species of bats often use the same roost; thus, a roost containing mostly non e ndangered species may also harbor endangered ones (Hill and Smith, 1984; McCracken, 1989). This lack of knowledge regarding the status of bat populations emphasizes the real need for precautions around roosts of all bats (Stebbings, 1980). As an additional precaution, we recommend that any species of cave dwelling bat be treated as though their populations are in decline; exceptions should be limited only to those cases for which substantial evidence exists to the contrary.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 37 Recommended Guidelines 1. Avo id revealing exact locations of bat roosts. Many bat specialists have already adopted this practice, often after declines in populations, damage to roosts, or both, have taken place soon after a publication revealed the roost location. 2. Caves or other s tructures designated as critical habitat for endangered or threatened species should not be entered except by federal or state management biologists or researchers with valid permits when bats are present. 3. Caves protected by fences or gates should not be entered except by special permit holders, regardless of species of bat present. 4. Caves protected by warning signs about bat nurseries or hibernating bats should not be entered during the times of year specified on the sign. Entry can be permitted at those times of year when bats are not present, so long as the cave is left unaltered and unpolluted. colonies of endangered or threatened bats should not be visited, unless there is a special need and a fe deral permit has been obtained. Maternity colonies of non endangered or non threatened bats generally should not be disturbed. It is highly recommended that if maternity colonies must be visited that it be done at night while the adults are away from the r oost. 6. For bats whose populations are either known or suspected of being in decline, most field research, including banding, should be discontinued while the bats are hibernating. Even for monitoring purposes, disturbances should be as brief as possible and should occur no more than once per winter, preferably in alternate years. In general, winter banding efforts for any bat population should be minimal and clearly warranted because arousing bats to band them can cause excessive mortality. 7. Persons e ntering bat roosts should reduce their impact by minimizing noise and the number of participants. Lights should be limited to those powered by batteries or cold chemicals such as cyalume. Persons should avoid passing too closely to roosting bats, and shoul d leave no refuse or other signs that they were there. 8. Research on federally listed bats should be carried out through stringent adherence to the terms of federal and, when applicable, state permits. 9. Persons collecting bats need to be aware of fede ral and state laws governing the collection and transportation of bats, and must be in possession of the appropriate scientific collecting permits before the study is undertaken. When bats are collected for laboratory research, proper handling and transpor tation of captured animals should be practiced to minimize injuries and/or deaths, and therefore the actual numbers taken from a roost. 10. In nearly all cases, collecting should be done at, near or outside roost entrance rather than inside the roosts. Co llecting is usually done with harp nets placed at or near roost entrances or with mist nets placed outside roost entrances. A limited amount of collecting can be safely done inside large cavern systems or in some man made structures. Collectors should avoi d captures in excess of numbers needed by estimating the size of colonies before setting up nets. 11. Collections should be minimal, including only a small fraction of the population of any given colony, should not be redundant with existing collections, and should be sufficiently infrequent to ensure that healthy colonies are sustained. Collecting should only be done as a means of furthering our knowledge and understanding of bats and not just because the bats are there. 12. Collecting should be done so as to avoid any damage to the cave or other roost structure. 13. Firearms, open flame torches, smoke or toxicants (including pesticides) should never be used inside bat roosts. 14. Despite their genetic, ecological and economic importance, bats have an i mage problem and are not popular with most of the public. Current public attitudes towards bats threaten their survival, especially since the first reaction of most people to their presence in houses or buildings is to eliminate or remove them as quickly a s possible (Hill and Smith, 1984). Because popularity is a major stimulus for conservation, we recommend that wildlife agencies, spelunking societies, colleges and universities, and nature centers, in conjunction with bat specialists if possible, increase their efforts to educate the public about bats. These efforts could include newspaper and magazine articles and talks directed at school


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 38 children, conservation groups, spelunking clubs and land owner groups. In addition, we recommend continuing education p rograms dealing with bats be directed at wildlife managers, conservation officers, wildlife commissioners, animal damage control agents and veterinarians. Adequate protection for bats may be next to impossible without an educated public (Tuttle, 1979). Thr ough such education efforts, the public can be made more receptive to restrictions on human activities in or near bat roosts. 15. Although many of the guidelines proposed herein call for various permits for research, we do not imply that merely holding pe rmits will ensure against detrimental effects of study. The American Society of Mammalogists expects that scientists will maintain high professional standards when conducting research in and around bat roosts. 16. We recognize that special circumstances m ay require these or any other guidelines to be violated for the welfare of an endangered or threatened species. Decisions on such matters will have to be made on an ad hoc basis by bat specialists and recovery team members in conjunction with the appropria te wildlife agencies. We intend these guidelines as general guidelines only, subject to modification under extenuating circumstances or as new information becomes available. Acknowledgment s We would very much like to thank B. S. Clark, M. J. Harvey, T. H. Kunz, J. L. Patton, R. M. Timm, M. D. Tuttle, B. J. Verts, K. T. Wilkins, D. E. Wilson, and two anonymous reviewers for their helpful suggestions on improving these guidelines. Literature Cited Barbour, R. W., and W. H. Davis. 1969. Bats of America. Unive rsity of Kentucky Press, Lexington, 286 pp. Gillette, D. D., and J. D. Kimbrough. 1970. Chiropteran mortality. Pp. 262 283, in About bats: a chiropteran biology symposium (B. H. Slaughter and D. W. Walton, eds.). Southern Methodist University Press, Dallas , Texas, 339 pp. Gunier, W. J. 1971. Stress induced abortion in bats. Bat Research News, 12:4. Hill, J. E., and J. D. Smith. 1984. Bats: a natural history. University of Texas Press, Austin, Texas, 243 pp. McCracken, G. F. 1989. Cave conservation: special problems of bats. National Speleological Society Bulletin, 51:47 51. Mohr, C. E. 1972. The status of threatened species of cave dwelling bats. National Speleological Society Bulletin, 34:33 47. Stebbings, R. E. 1980. An outline global strategy for the cons ervation of bats. Pp. 173 178, in Proceedings of the Fifth International Bat Research Conference (D. E. Wilson and A. L. Gardner, eds.). Texas Tech University Press, Lubbock, Texas, 434 pp. Thomas, D. W., M. Dorais, and J. M. Bergeron. 1990. Winter energy budgets and cost of arousals for hibernating little brown bats, Myotis lucifugus . Journal of Mammalogy, 71:475 479. Tuttle, M. D. 1979. Status, causes of decline, and management of endangered gray bats. The Journal of Wildlife Management, 43:1 17. -199 1. How North America's bats survive the winter. Bats, 9:7 12. Prepared by the Protection of Bat Roost Guidelines subcommittee, Steven R. Sheffield, James H. Shaw, Gary A. Heidt, and Leroy R. McClenaghan, of the Conservation of Land Mammals Committee. These guidelines were approved by the Board of Directors on 21 June 1987 at their annual meeting in Albuquerque, New Mexico.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 39 On Cave Gates Kennedy, J. 2006. Pp. 147 165, in Cave Conservation and Restoration (V. Hildreth Werker and J. Werker, eds .). National Speleological Society, Huntsville, Alabama. 615 pp. : In this chapter, dimensions for materials deviate from the standard metric/English format used elsewhere in this volume because construction materials are usually sold in English units i n the United States. Cave gates. There are hardly two words that polarize cavers as much as these. Even the most vocal anti gate cavers admit that gates serve an important function in protecting irreplaceable cave assets, and in reducing the liability o f cave owners. Yet all too often land managers turn to gates as quick and easy solutions to complex cave management problems. Cave gates can be an important part of a comprehensive cave management plan, but there is much more to gating a cave that just w elding steel. This chapter will not tell you everything you need to know about gates and gating, but it will give you an overview of the planning, design, building, and monitoring process and will direct you to additional expert resources. Is a Gate Ne eded? First, determine if a gate is truly necessary. Since a gate is a somewhat permanent structure that requires great expenditures of resources and may negatively impact the cave environment, it should be installed only after careful planning and design . Other protective methods may be more efficient or effective and should be explored first. Other protective measures for cave habitats include but are not limited to the items in the following list. directing trails While carefully designed and constructed gates have minimum effect on the cave environment, poorly placed gates can be very detrimental to the cave and its resource s. If a gate is needed, it should have minimum impact on the cave. : If a cave gate will change air currents that originally flowed through breakdown or small openings, then measure the natural airflow before the gate installation begins. De sign and construct the gate to mimic the original airflow. (See virgin digs, page X265.) Types of Protective Closures Next decide on an appropriate gate design. In this section, the term cave gate is used for any type of lockable barricade that prevents human access to the cave, including fences, doors, and bars. Some types of closures, such as a simple chain across a passage restriction, are less secure than others. The majority of this chapter focuses on various types of bat friendly horizontal bar ga tes, which are suitable for most situations and are very secure. In rare instances that require an environmental seal, such as a newly opened cave or section of cave with no natural entrance, bat friendly gates would be inappropriate. In those cases, air l ock gates may be necessary to prevent drying air currents and contamination by outside organisms or materials such as mud. Bat Friendly Gates Most cave gating scenarios call for a bat friendly gate. Fortunately, there are many types of gates that incorpo rate bat friendly features. Standard bat friendly gates are designed wi th widely spaced uprights and 5 3/4 inch (146 millimeter) spacing between horizontal bars. The actual design depends on the amount of human vandalism pressure, the bat species present, a nd the way the bats use the cave. For instance, we must be aware that some species of bats do not tolerate cave gates at all, and others only at certain times in their life cycle. The size and angle of the cave entrance may also dictate innovative adaptati ons of the standard bat gate designs. (See drawings for the horizontal bar gate, figure 3.) After carefully choosing a location and initiating the actual construction, observe the effectiveness and impact of the gate over time. If the gate is creating ne gative impacts, quickly modify or remove it. Routine maintenance tasks should be planned before commencing the actual construction. Maintenance schedules may be required to repaint the gate if necessary, remove sticks and leaves or flood debris,


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 40 change loc ks before they stop working, and remove rocky debris that accumulates around the gate. Signs, fences, and gates are also susceptible to vandalism, and repairs or replacement may be necessary. Selection of Protection Method Before installing a gate at a cave entrance, many factors must be considered. Issues to examine can be divided into two broad categories. Evaluate the cave resources themselves. Assess the level of threat to the cave resources. Obviously, an easily accessible cave is more in need of protection than a rarely visited cave in a remote wilderness area. Likewise, a cave with a wealth of speleothems, important biota, or archeological and paleontological remains, is more in need of protection than a small, featureless, relatively sterile cave. We believe that all caves have value. But how do we determine what is significant and threatened? Ideally, a complete resource inventory is done for the cave in question, with periodic monitoring up to the time of the actual gating. In reality, th is rarely happens. Even caves that have been known and visited for decades hardly ever have simple baseline data, like temperature and invertebrate studies. Often a gate is planned because the cave owner or manager is reacting to a crisis the discovery o f a rare and threatened resource, advanced loss of cave resources, sharply increased visitation, or liability concerns. No matter what the impetus for protection, we should consider all users and resources when designing a gate or other type of protective closure. Five Possible Scenarios This process can be illustrated by a hypothetical example. Assume that we have five caves on a 1,000 acre (405 hectare) parcel of land. Cave 1 . This cave is located on a remote back corner of the property, accessible o nly by fording a shallow river. It is backed by several hundred contiguous acres of forest under other ownership. It has a few thousand feet of passage, some fun climbs, and ancient bear den sites. Cave 2 . This is a shallow, 25 foot (8 meter) pit leadin g to 300 feet (90 meters) of easy canyon and crawlway. This cave is very near a road, and an obvious trail leads to its entrance. No bats or other obvious wildlife have been noted, but the temperatures are very cold, even in the summer. Cave 3 . This cave is on a distant hillside and has a small obscure opening that leads through breakdown and crawls to a fairly large room. Endangered bats hibernate in this cave during the winter. Cave 4 . This is a large, well known system with several horizontal entranc es. Several entrances have obvious trails leading to them, and one entryway is small, torturous, and rarely used. There are many delicate and unusual speleothems in this cave, and damage has been steadily increasing for many years. Cave 5 . This is a smal l crawl cave with records of endangered invertebrates. Because it is near the fourth cave, it is often mistaken as an entrance to Cave 4 and receives unnecessary traffic. What to do with these? Gating all the entrances would be time consuming and expensiv e, would likely aggravate those people currently visiting them, and might cause overflow problems in neighboring caves. We already have some resource information on the five caves, so we can prioritize their significance. We also have information on the le vel of disturbance and threats to these caves, so we can determine the level of urgency for protecting each one. Now we have to determine exactly how we will protect each cave. Cave 5. This cave appears to have an urgent need for protection because of it s endangered fauna and the unintentional traffic. This reality would need to be weighed against the population size of the invertebrates, and the numbers of those species in other caves. Since this is a relatively small cave with a well Cave Significance Threats 1 paleontology, recreation, pristine few due to difficult access 2 possible bats in winter, recreation highly visible, liability (pit) 3 bats in winter small, hard to find, rarely visited 4 recreation, speleothems, possible invertebrates heavy traffic, increasing damage 5 Invertebrates unintentional traffic from Cave 4 Table 1 . Set Up a Table to Prioritize Actions


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 41 known entrance and no bats, a gate could be appropriate. Cave 4 . This cave needs a more thorough resource inventory. Its proximity to Cave 5 indicates a likely connection. Although it is viewed primarily as a recreational cave, the possibility of finding endangered invert ebrates there is high. There are too many unknowns at this time to make a good decision. Perhaps the entrances can be gated. A small internal gate might allow access to only part of the cave. Signs and a permit system might reduce the number of visitors to a sustainable level. We need to know more. Cave 3 . This cave might be categorized toward the opposite end of the spectrum. Rarely visited and obscure, it faces no immediate threats. The only critical time of year is winter when the bats are hibernating . Winter visits could be curtailed simply by doing public education through the local grottos. Because the entrance is obscure, a gate or signs might draw unnecessary, detrimental attention to the cave. Cave 2 . This cave presents a different challenge. I t is easily accessible and well known, so rerouting the trail would make little difference. A combination of educational signage and a bat friendly fence could prove beneficial, and would not detract from the aesthetics of the pit. If the fence is repeated ly damaged, and if the cave is suitable for bats, a cupola style bat gate could be installed over the entrance (Figure 4). Since temperatures are suitable for hibernating bats, we might conclude that bats are no longer in that cave due to disturbance, so f encing or gating should allow for their eventual re colonization. A thorough in cave survey for old guano or roost stains would help with this decision (Figure 1). As with any site where there is a strong history of visitation, the reputation for open acce ss must be broken, even if it means patrolling the site and arresting violators. Cave 1 . This is a relatively pristine wild cave. However, traffic may increase if other nearby caves are gated. The paleontological resources are very vulnerable. A permit s ystem, combined with increased caver education, might work here if the location is protected by the terrain and the remoteness of the site. If natural site protection is not adequate, the cave might need a gate. Since the threats are not immediate, protect ive efforts for this cave are not as urgent. Summary of Assessment necessary before installing any protective device on a cave particularly more permanent structures like gates. Public input from c oncerned user groups should be solicited, especially if those groups oppose closure and may damage or destroy protection efforts. It is essential that gates and other protective structures be continually monitored, not only for structural damage, but als o for their impact on the cave ecosystem. Gates, culverts, or fences that cause a negative effect should be modified or removed. Cave gating is not a quick Band Aid approach to cave management. Gating is merely one tool a cave manager can use. Maintenance schedules should be established because gates need attention and review after installation. Certain types of protective efforts may have an opposite effect than that intended. For instance, several species of North American cave dwelling bats do not tole rate any type of gate at all. Some species only tolerate gates during one part of their life cycle and not at other times of the year. Always consult experts early in the planning stages of any gating project and be sure to get the most current gate desi gn recommendations through Bat Conservation International, the National Speleological Society, and the American Cave Conservation Association. Figure 1. Bat roost stains on cave walls provide evidence of bat population even when bats are not present. In the image, a 3 inch (80 millimeter) HOBO® P ro data logger is used for scale. (See page 5 of color section.) © Merlin D. Tuttle, BCI


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 42 Location and Design Placement of a fence or gate is as critical as the actual design of the structure. Poor ly located gates may increase flood damage to the cave, accumulate debris and restrict airflow, and restrict movement of bats or other wildlife. Poorly placed gates may also be more susceptible to natural damage or vandalism, and may increase predation at the cave. Much depends on the size, shape, and orientation of the opening, but in general, bat gates should not be situated in natural passage constrictions, and fences should not interfere with the flight path at the entrance. It must be stressed that cave gating is not a cookie cutter management technique. Simply because a cave has bats does not mean that one can dust off a gate design and build it in the cave mouth. But even if a cave does not have bats, the cave may need a bat friendly gate. The appr oach to protecting each cave should be based on the configuration of the cave itself, the species using it, the season bats occupy it, the proximity to civilization, and so on. There is not a one size fits all solution to cave protection. Poor gate desig n or placement can render the cave unsuitable for bats. Consult the experts listed in the resources section at the end of this chapter. Gate Location As mentioned above, cave gates should not interfere with the natural flow of air, water, nutrients, or wildlife to and from the cave. Gates should never be in a constricted part of the passage. The bottom of an entrance slope should also be avoided since it will catch debris that will pile up against the gate. In cave entrances that have inflowing streams this can be a very serious problem. The gate on the North Entrance of Bat Cave (Carter County, Kentucky) failed in the spring of 1996 as flood debris lodged against the gate, backing up water until the increased pressure finally collapsed the gate. The res ultant flood pulse destroyed many low roosting Indiana bats, a federally listed endangered species. (See Indiana bats, page X57.) Predation Dangers Predation can also increase dramatically because of badly located gates. Most bat predators rely on vision when hunting, so gates in the daylight or twilight zone bats slow down to negotiate the gate bars, or back up behind the gate waiting their turn to pass through, they are easily captured by enterprising ra ccoons, ringtails, and feral cats. Gates installed beyond the twilight zone eliminate the the lower entrance of Sinnett Thorn Mountain Cave (Pendleton County, West Virginia) had piles of Virginia big eared bat wings around it from the nightly predations of local house cats. The gate was removed in October 1998 and a new gate was built in a tall area approximately 75 feet (23 meters) further in, despite having to maneuver the steel and equipment through a crawlway. The new gate, in the dark zone, has eliminated the predator problems. Cupola or Cage Gates for Vertical Entrances Figure 2 . This is a poorly designed gate, constructed of 1 inch (25 millimeter) round bars. It is not very secure the bars maybe easily bent and the welds are small . The small rectangular openings in the narrow vertical entrance make the gate difficult for bats to fly through. On this type of platform gate constructed in a vertical entrance, branches and leaves can collect to restrict airflow and light. © 1989 Jim Ke nnedy, BCI


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 43 Vertical or near vertical entrances pose their own set of problems. A horizontal gate at such an entrance accumulates debris, makes a perfect f eeding platform for predators, and is very difficult for most bats to negotiate. To solve these problems, a raised gate called a cupola gate or cage gate can be used. Generally, the longer and narrower the opening, the larger and taller the cupola gate should be in order to give the bats adequate space to gain altitude and avoid predators. Cupola gates are not practical for very large openings, and f encing may be the only option. For vertical entrances with very short drops, a standard gate may be instal led deeper within the cave where the passage begins to be more horizontal (when the vertical entrance itself is not a liability concern). A recent innovation, since the late 1990s, is the chute gate, sometimes called a window g ate. An otherwise standard horizontal gate is modified with a rectangular opening boxed in with additional angle iron and expanded metal mesh. This design allows sufficient opening for emerging bats and makes it very difficult for trespassers to breach the opening. The chute is usually angled to make it more difficult for humans to enter. This particular gate design is especially useful in caves with large bat populations, such as gray bat maternity colonies, which have entrances that are too small for trad itional half gates or flyover gates. Because of the weight extending out from the main (standard) part of the gate and the resulting mechanical stresses, extra attention is needed in the design and construction to prevent future cracked welds and gate fail ure. Chute gates have been used successfully on numer ous Alabama, Kentucky, Missouri , and Tennessee caves, and are well accepted by bats. Figure 5 . Chute gate at McDowell Cave, Missouri © 2001 Sheryl Ducummon Figure 4. A cupola or cage gate is often used in vertical or near vertical entrances.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 44 Figure 3 . Idealized sequence of horizontal bar gate construction, front and side vi ews. 3a . Measurements of the gate taken at regular intervals from a horizontal (level) line. 3b . Scale drawing of finished gate, used to estimate materials. 3c . Trenching and securing of sill


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 45 3d. Installation and securing of uprights. 3e. Installation of bottom bar and hangers for second bar. 3f. Continuation of hangers and horizontal bats (for clarity, removable bar is not shown).


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 46 3g. Completion of horizontals. 3h. Placement of bat guards. 3i . Completed gate


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 47 Nonstandard Gates Caves that are entirely unsuitable for bats (as opposed to sites where bats a re not currently found) may be candidates for gates that are not bat friendly. However, the bat friendly design is the preferred solution for most caves, except those that have no natural entrance and require some sort of environmental seal. Sometimes the availability of materials and volunteer labor, or the lack of adequate funds will dictate construction of a nonstandard (not bat friendly) gate. Nonstandard gates are almost always poor substitutions. Educational Signage All finished gates require signs stating the purpose of the gate and contact numbers for more information. The penalty for entering the cave or vandalizing the gate can be written in small print, but this should not be the focus of the sign because it is often taken as a dare by would be vandals. Educational material is less antagonistic. or are needlessly damaged by thwarted cave visitors. Permanent signs mounted inside the gate where they can be read, but are out of harms way, will last longer. Paper and wooden signs are highly susceptible to weather, decomposition, and the gnawing teeth of rodents. Metal or plastic signs are preferred. (See protecti ve signs in caves, page X187.) Construction Logistics This cave gating chapter is no substitute for a more complete cave gating manual or training workshop. While it covers the rudiments of cave gating to assist resource managers in making better informed decisions, it is too brief to help with actual design and installation. Neverthel ess, here we provide information for better planning of gating projects. Further assistance is readily available on request. (See cave gating resources, page X168.) Timing Construction should take place during seasons when human activity is least disturb ing to the cave resources. For bat caves, this means the work must be done when the bats are absent. Some caves may be used as both summer and winter roosts, which leaves only short periods Figure 9. e the removable bar at bottom right. Expanded metal mesh covers the overhanging top portion, making it extremely difficult to climb over. Coating the overhang with grease also helps repel trespassers. © 1997 Keith Christenson, BCI


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 48 Figure 7. (middle) Hor izontal bar spacing, typical detail (not to scale). Figure 8 . (bottom) Stiffener detail horizontal bars (not to scale). Figure 6 (top). Typical bat gate (not to scale).


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 49 in the spring and fall for construction. Seasonal temperatur e variations may also cause reversals in the necessary to install temporary plastic curtains inside the construction site to keep smoke and noxious welding fumes out of the cave. (See toxic fumes, pa ge X49.) Materials Ordering adequate materials depends on accurate estimates of the area to be covered. Gate construction projects require accurate measurements and scale drawings of the finished gate. Materials should be ordered well in advance of the actual gating and may need to be stored off site in a secured area before being transported to the cave. Always order a little extra for emergencies. Supplies To help ensure completion of the project, carefully calculate welding gases, welding rods, grin ding wheels, and other expendables. It is much easier to return unused supplies, or save them for the next project, than to run out before the new gate is finished. Tools The remoteness of the site will dictate the type of tools needed, but almost every gating project requires an electric generator or two to run the welders, grinders, and lights. Most projects need the following equipment. acetylene torches (with spare tips and regulators) mmers and wire brushes clamps held grinders Also, provide the following safety equipment at cave gating sites. Always plan for things to break, so have backups on site or readily available. Other equipment such as come al ongs, pulleys, chainsaws, all terrain vehicles, or in extreme cases, a helicopter may be needed to move materials to the site. Short, 8 foot (2.5 meter) lengths of 1 inch (25 millimeter) tubular nylon webbing tied in loops make excellent carry handles fo r moving lengths of steel. Tools should be color coded or labeled so they get back to their proper owners. Be careful to keep track of tools and equipment. Tools are especially easy to lose in or around the cave area. Transportation of Materials Many ing enious methods have been developed for moving materials to cave sites. Rarely can the delivery truck drive to the cave mouth. For long hauls, caver power may suffice, given a large enough workforce. Animal power (horses, mules, and burros) is sometimes use d. All terrain vehicles are sometimes used in non wilderness areas with adequate trails. Boats or rafts may be necessary along rivers or lakes. Materials may even need to be airlifted in extremely rugged terrain. Airlifts are sometimes accomplished with the cooperation of a local military reserve unit (the project may be used as a training mission). But during the course of most projects, all materials must be carried by hand. Keep in mind that a 20 foot (6 meter) length of 4 inch (10 centimeter) angle ir on, 3/8 inch (9.5 millimeter) thick, weighs about 196 pounds (89 kilograms). Avoid pinched fingers and crushed toes by keeping safety in mind. Personnel The gate designer should oversee construction this person is most important in any gating project. C urrently, there are very few people in North America with the experience needed for all but the simplest jobs. (See contact list, page X170.) Next comes the welder, who may be an agency employee, a volunteer, or a person hired specifically for the projec t. Depending on the size of the gate and the amount of work necessary, it is usually good to have several welders (people and machines) available to make the work go faster and to offer rest breaks. Gating projects also need one or more welding assistant s, anticipating the next piece to be cut, handing tools, taking measurements, and generally facilitating the workflow so that no one is standing around idle.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 50 Finally, a project needs sufficient labor to prepare the site, carry items from the cutting area to the gate location, carry the steel from the drop point to the work area, and clean up afterwards. These workers can be hired with the welder, be provided by the responsible agency or organization, or be volunteers such as local cavers. In several gat ing projects, prison labor was arranged for much of the heavy work. Using volunteers is educates them about purposes for the gate, and lessens potential for opposition and future vandalism to the gate. ake care of the safety and well being of your workers. Provide plenty of food and drinks, and give adequate recognition after the project is finished. Safety Every cave gating work plan needs to address the protection of the cave and s urrounding site as well as the safety of the workers involved. Prevent ground fires from starting at the work site. It may be necessary to temporarily remove dead leaves or grasses in the areas where cutting, welding, and grinding occur. As a precaution, h ave plenty of water and fire fighting tools (rakes and shovels) on hand. An Indian Pump or chemical fire extinguisher is also handy. All workers should wear leather work boots, preferably steel toed, as well as leather gloves, hardhats (caving helmets ar e fine), long pants, long sleeved shirts or coveralls, protective eyewear, as well as hearing protection, especially when working around the welders, torches, and grinders. Caution all workers not to look directly at the torch flame or welding arc. Brief t he crew on hot metal, heavy objects, potential dangers from the tanks of welding gases, and any other hazards specific to the site (loose rock, steep slopes, poison ivy, and the like). Keep a well stocked first aid kit on site. Also, be aware of the danger s of exhaustion, dehydration, hypothermia, and heat related illnesses. Be sure the team takes breaks, eats during the day, and keeps hydrated. Site Restoration It may be difficult, but try to minimize disturbance of rocks, vegetation, and ground cover d uring steel hauling and other work. Natural contours should be restored after the gating is completed, unless the work on the cave entrance includes retuning it to a former historic configuration in an attempt to restore internal conditions. Sites may need re vegetation, and trails may need to be blocked to divert casual hikers from the cave. All trash should be picked up and removed, including all scrap metal and as much welding waste as possible, including welding rod stubs. Cave gates, after painting (if necessary), should blend in rather than attract attention. If an entrance was previously modified or enlarged, gating processes may provide a perfect time to restore the entrance to a former ecological state. Keep in mind that, relatively speaking, cave s are short lived geologic features that constantly change. Entrances open and close naturally during the life of some caves, sometimes repeatedly. Choosing the historic baseline configuration is sometimes a judgment call based on the special resources f or which the site is actively managed. For declining populations of endangered Indiana bats, for instance, we would aim for restoration to a time frame of pre European settlement, but post Pleistocene. Locks and Removable Locking Bars Since the main purp ose of a cave gate is to secure the site from intrusion, the choice of locking mechanism is critical. Many modern gates now dispense with hinged doors entirely and use removable locking bars. The removable bars can be secured with standard padlocks or with specially keyed bolts, similar to automotive locking lug nuts. Removable bars have several advantages. tasks. All padlock mechanisms must be designed to protect the lock from damage. Locks should be inspected regularly and replaced at the first sign of trouble or failure. No gate is completely vandal proof, but the idea of building a strong gate secured by a weak lock is ridiculous. If the cave is worth gating, make it as secure as possible. Monitoring and Maintenance So, you have finished building the gate and restored the entrance zone to a natural appearance. Job well done, right? More like job half done. There are no guarantees that the gate will accomplish your objectives despite your most careful planning.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 51 ecosystem, a gate may cause further problems. Only long term monitoring and assessment will t ell. For bat caves this entails nightly and seasonal observations to uninterrupted. For other critters, monitoring might involve population estimates via specific sampling techniques. Monitoring requir ements also point out the need to establish good baseline data before gate installation so comparisons can be made with post gating data. At the minimum, temperature and airflow should be recorded, but observations of moisture and humidity, animal distribu tion, and nutrient flow are also useful. If the gate is not doing its job, then it should be modified or removed. Many bat caves gated in the 1970s and early 1980s were thought to be protected and were largely ignored thereafter. Continuing bat populatio n declines puzzled researchers, who believed the caves were protected and looked for other reasons to explain decreases. Recent advances in gating knowledge show that the gates themselves were causing negative impacts on the caves because they were poorl y designed or placed, or because the entrance was modified during the gating process. In an extreme case, the temperature of the cave was raised by as much as 5°F (2.8°C). Temperatures were restored and the population began to increase when the original ga te was replaced with a better positioned and better designed closure. Monitoring programs are now initiated early in gating projects to identify and correct bad situations before human modification results in tragedy. Gates must also be monitored for the inevitable breaching attempts. Certain segments of our society delight in trying to break into places where access is denied. Proper signage will go a long way toward educating most of the public about the reasons the cave was gated. Signs should point vi sitors to more information and contacts for access. Gaining the trust and cooperation of user groups and local cavers during the planning and construction processes will also alleviate potential animosity and break in attempts. Repairing Damage Any damag e to the gate should be repaired immediately otherwise, you will be repairing more damage and dealing with illegal entries. When design flaws and weaknesses are discovered, you have the obvious opportunity to modify the gate and make it stronger. As noted not to negatively impact the cave environment with security modifications. Recurring vandalism may require increased security measures, such as surveillance. Sometimes trustworthy local cavers can be named as volunteer cave stewards who can provide much needed manpower for patrolling the site. A well publicized arrest of trespassers vandalizing a posted cave gate makes a wonderful deterrent to other would be lawbreakers . Many other clever techniques have been utilized to deter vandalism, including fake monitors and signs announcing (usually nonexistent) alarm systems. Real alarms can also be used, triggering a dispatch to the agency office or local law enforcement author ities. Cave Gating Resources If, after reading this, you feel overwhelmed and want to stay as far away from cave gating issues as possible, RELAX! There are several sources of excellent assistance available to help you. Modern, bat friendly cave gates (a lso called zero airflow reduction bat gates) are the result of many years of experimentation and development, supplemented by field observation, strength testing, and wind tunnel testing. The design presented in this chapter is the standard accepted by m ost federal and state agencies that manage caves, and by organizations such as The Nature Conservancy and Bat Conservation International. The leading force behind bat friendly gate development has been the American Cave Conservation Association, particular ly Roy Powers. Detailed drawings may be requested from them. Across the country, there are examples of many adaptations showing varying degrees of success. Successful gate designs provide entrance security and avoid the blockage of airflow, water, nutrient s, and animals. Current Books on Cave Gate Design Bat friendly gate designs are also widely used for closing abandoned mines. Mines and caves are similar, but not equivalent management concerns. Mines usually lack the complex ecosystems and recreational values that caves offer, and mines often pose bigger liability problems. Mines are extremely short lived in comparison to caves. Stabilizing or closing mine entrances to achieve desired conditions does not have the ramifications that such actions cause in undisturbed caves. Bat Conservation International (BCI) has


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 52 produced a free booklet, Bats and Mines, that discusses in detail the suitability of mines as habitat, addresses the dangers associated with them, and includes full plans for both standard and cup ola gates. The booklet also offers excellent template forms for conducting external and internal summer and winter bat site assessments. (In the additional reading list for this chapter, see Tuttle and Taylor 1998.) The authors and editors know of no mod ern, comprehensive, published gate plans for caves that have no bats or other vertebrates. Trap door gates and air lock gates are common in several parts of the United States but are usually built by local experts. A detailed book on cave gating has been developed by the US Fish and Wildlife Service, the USDOI Office of Surface Mining, Bat Conservation International, the American Cave Conservation Association, the National Speleological Society, and numerous other sponsors. It includes the entire proceedi ngs from the groundbreaking conference on cave and mine protection options held in Austin, Texas, in March 2002. It is available through the National Speleological Society and covers the entire gating process in detail. (In the additional reading list for this chapter, see Vories and others 2004.) Cave Gating Seminars To get hands on training, participate in one of the Cave Gating Seminars cosponsored by the American Cave Conservation Association, Bat Conservation International, the US Fish and Wildlife S ervice, and the USDA Forest Service. These workshops combine evening slide lectures and discussions with hands on gate building experience. The small group residential setting teaches design and placement philosophy, covers design options and case studies, and offers an opportunity to interact with some of the most knowledgeable cave gaters in the country. Contact the American Cave Conservation Association or Bat Conservation International for dates and locations of upcoming workshops. Cave Gate Contracto rs There are also several private individuals and firms that will contract gate building projects. The best of these have many years experience or are graduates of the Cave Gating Seminar. Names of those known to be knowledgeable and reliable can also be obtained from Bat Conservation International or the American Cave Conservation Association. (See the contact list at the end of this chapter, page 170.) Summary Cave gating is only one form of cave protection. It should not be undertaken without sufficie nt study and planning. There are many types of gates and the manager should choose the type that best protects the resources within the cave and best fits the cave configuration. Planning, construction, and follow up activities are time and resource inte nsive. Gating projects may require a lot of manpower and other resources, including volunteers as well as specialized equipment. There are several sources of expertise and possible funding assistance for gating projects. Gating experts should always be con tacted before any work begins. Additional Reading Anon. 1985. Volunteers protect Tennessee bats. American Caves 1(2):8 9. Anon. 1993. James Cave receives new gates for bats. Bats 11(3):4. Anon. 1993. BCI helps protect Pennsylvania mine for bats. Bats 1 1(4):16 17. Anon. 1995. New ACCA gates protect Kentucky and Tennessee caves. American Caves 8(1):10 11. Anon. 1997. Gates, gates, and more gates! American Caves 10(1):6 7. Bat Conservation International (BCI). BCI home page. . D irect link to full articles from Bats Online. . Accessed 2004 March 30. Bobo K, Greene J. The gating of Wolf River Cave. NSS News 58(10):283, 286, 294. Brady JT. 1985. Cave management for the endangered Indian a bat (Myotis sodalis) and gray bat (Myotis grisescens). In: Thornton H, Thornton J, editors. 1982 Cave Management Symposia Proceedings. Richmond (VA): American Cave Conservation Association. p 86 95. Brown CB. 1996. Bat habitat in caves: What are the cav responsibilities? NSS News 54(2 3):52 53. Burghardt JE. 1997. Bat compatible closures of abandoned underground mines in National Park System units. In: Brandt JE, editor. 1997 Proceedings of the American Society for Surface Mining and Reclamation. Le xington (KY): American Society for Surface Mining and Reclamation. p 184 195. Currie RR. 2002. Response to gates at hibernacula. In: Kurta A, Kennedy J, editors. The Indiana Bat: Biology and


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 53 Management of an Endangered Species. Austin (TX): Bat Conservati on International. p 86 99. Dutko R. 1994. Protected at last, the Hibernia Mine. Bats 12(3):3 5. Elliott WR. 1996. The evolution of cave gating. American Caves 9(2):9 15. Elliott WR. 2001. Project reports 2000: Missouri caves. American Caves 14(3):6 9. Elliott WR. 2001. Cave Gating Criteria. Unpublished document for the Missouri Department of Conservation. 5 p. Fletcher MR. 1985. Endangered bat protection at Buffalo National River, Arkansas. In: Vandyke JE, editor. 1984 National Cave Management Symposiu m Proceedings. Missouri Speleology 25(1 4):147 150. Forbis S, Haskins V, Foster DG. 1996. Protecting the ancient history of Crumps Cave. In: Rea GT, editor. 1995 National Cave Management Symposium Proceedings: Spring Mill State Park, Mitchell, Indiana, Oc tober 25 28, 1995. Indianapolis (IN): Indiana Karst Conservancy. p 88 92. Hathorn J, Thornton J. 1987. The common sense guide to cave gates. In: ACCA Cave Management Series 1(3):23 45. Horse Cave (KY): American Cave Conservation Association, Inc. Hathorn J, Thornton J. 1993. Cave gates: design and construction considerations. In: Foster DL, Foster DG, Snow MN, Snow RK, editors. 1991 National Cave Management Symposium Proceedings: Bowling Green, Kentucky, October 23 26, 1991. Horse Cave (KY): American Cave Conservation Association, Inc. p 359 363. Hopper HL. 1999. Cave gating: three success stories. American Caves 12(3):6 9. Hunt G, Stitt RR. 1975. Cave Gating. Huntsville (AL): Cave Gating (2nd edition ). 1981. Huntsville (AL): National Speleological Society. [Use these books for historical reference only gate designs are outdated.] Ludlow ME, Gore JA. 2000. Effects of a cave gate on emergence patterns of colonial bats. Wildlife Society Bulletin 28(1):1 91 196. MacGregor J. 1993. Responses of winter populations of the federal endangered Indiana bat (Myotis sodalis) to cave gating in Kentucky. In: Foster DL, Foster DG, Snow MN, Snow RK, editors. 1991 National Cave Management Symposium Proceedings: Bowling Green, Kentucky, October 23 26, 1991. Horse Cave (KY): American Cave Conservation Association. p 364 370. Martin KW, Puckette WL, Hensley SL, Leslie DM Jr. 2000. Proceedings of the Oklahoma Academy of Science 80:133 137. Murphy M. 1993. Restoring Coach Cave. Bats 11(3):3 5. Bats protected. American Caves 9(2):16 17. Olson R. 1996. This old cave The ecological restoration of the Historic Entrance ecotone of Mammoth Cave, and mitigation of visitor i mpact. In: Proceedings of the Fifth Annual Mammoth Cave Science Conference. Mammoth Cave (KY): National Park Service and Cave Research Foundation. p 87 95. Powers RD. 1985. General cave gate considerations. In: Thornton H, Thornton J, editors. 1982 Nation al Cave Management Symposium Proceedings. Richmond (VA): American Cave Conservation Association. p 77 79. Powers RD. 1993. Design improvements for gating bat caves. In: Foster DL, Foster DG, Snow MN, Snow RK, editors. 1991 National Cave Management Symposi um Proceedings: Bowling Green, Kentucky, October 23 26, 1991. Horse Cave (KY): American Cave Conservation Association. p 356 358. Powers RD. 1996. A study of acoustical confusion. In: Rea GT, editor. 1995 National Cave Management Symposium Proceedings: Sp ring Mill State Park, Mitchell, Indiana, October 25 28, 1995. Indianapolis (IN): Indiana Karst Conservancy. p 274 276. Quinn M, Petterson J. 1997. A grand effort in the Grand Canyon. Bats 15(3):4 7. Raesly RL, Gates JE. 1986. Winter habitat selection by north temperate cave bats. American Midland Naturalist 118(1):15 31. Richter AR, Humphrey SR, Cope JB, Brack V Jr. 1993. Modified cave entrances: thermal effect on body mass and resulting decline of endangered Indiana bats (Myotis sodalis). Conservation B iology 7(2):407 415. Roebuck BE, Vakili A, Roebuck L. 2001. Cave gate airflow disturbance: a qualitative study. In: Rea GT, editor. Proceedings of the 14th National Cave and Karst Management Symposium: Chattanooga, Tennessee, October 19 22, 1999. Chattano oga (TN): Southeastern Cave Conservancy. p 169 175. Roebuck L. 2000. Gating in Tennessee: a plethora of summer bat protection projects. American Caves 14(1):6 8. Stihler CW. 2000. Gates constructed to protect bats in West Virginia caves. American Caves 1 3(2):15 16. Toomey, RS III, Coburn ML, Olson RA. 2002. Paleontological evaluation of past use of caves by the Indiana bat: a significant tool for restoration of hibernacula. In: Kurta A, Kennedy J, editors. The Indiana Bat: Biology and Management of an En dangered Species. Austin (TX): Bat Conservation International. p 79 85. Tuttle MD. 1977. Gating as a means of protecting cave dwelling bats. In: Aley T, Rhodes D, editors. National Cave Management Symposium Proceedings: Albuquerque, New Mexico, October 6 10, 1975. Albuquerque (NM): Speleobooks. p 77 82 Tuttle MD, Stevenson DE. 1978. Variation in the cave environment and its biological implications. In: Zuber R, Chester J, Gilbert S, Rhodes D, editors. 1997 National Cave Management Symposium Proceedings: B ig Sky, Montana, October 3 7, 1977. Albuquerque (NM): Adobe Press. p 108 121.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 54 Tuttle MD. 1985. Joint effort saves vital bat cave. Bats 2(4):3 4. Tuttle MD. 1997. A Mammoth discovery. Bats 15(4):3 5. Tuttle MD, Taylor DAR. 1998. Bats and Mines. Resource Publication (Bat Conservation International) No 3. Revised edition. Austin (TX): Bat Conservation International. Tuttle MD. 2000. Where the bats are, Part III: caves, cliffs, and rock crevices. Bats 18(1):6 11. Tuttle MD, Kennedy J. 2002. Thermal require ments during hibernation. In: Kurta A, Kennedy J, editors. The Indiana Bat: Biology and Management of an Endangered Species. Austin (TX): Bat Conservation International. p 68 78. Twente JW Jr. 1955. Some aspects of habitat selection and other behavior of c avern dwelling bats. Ecology 36(4):706 732. Vories KC, Throgmorton D, Harrington A, editors. 2004. Proceedings of Bat Gate Design: A Technical Interactive Forum held in Austin, Texas, March 4 6, 2002. Carbondale (IL): USDOI Office of Surface Mining, Alton , Illinois and the Coal Research Center, Southern Illinois University at Carbondale. 434 p. Proceedings available on the internet . Accessed 2004 March 30. Werker JC. 2005. Materials considerations for cave installations. In: Hildreth Werker V, Werker JC, editors. Cave Conservation and Restoration. Huntsville (AL): National Speleological Society. p 171 178. White DH, Seginak JT. 1987. Cave gate designs for use in protecting endangered bats. Wildlife Society Bulletin 15:44 5 449. Contacts for Additional Information American Cave Conservation Association (Roy Powers or Dave Foster) PO Box 409 Horse Cave, KY 42749 0409 502.786.1466 ACCA Northwest Chapter (Jim Nieland) 1217 8 Lewis River Rd Ariel, WA 98603 9745 360.247.3946 360.247.3901 fax Bat Conservation International (Jim Kennedy) PO Box 162603 Austin, TX 78716 2603 512.327.9721, extension 17 512.327.9724 fax US Fish and Wildlife Service (Bob Currie) 160 Zillicoa Street Asheville, NC 28801 1038 828.258.3939, extension 224 828.258.5330 fax >


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 55 Does Competition for Roosts Influence Bat Distribution in a Managed For est? J. Mark Perkins Pp. 164 172. In: Barclay, R.M.R and R.M Brigham (Eds.) 1996. Bats and Forests Symposium, October 19 21, 1995 . Victoria, British Columbia, Canada. Research Branch, BC Ministry of Forests, Victoria. BC Working Paper 23/1996. ABSTRACT Previous studies disagree regarding the mechanism that determines distributions of neartic bat species. Many papers suggest that competition for foraging areas is important and is dictated by morphological characters or roost diversity. Here, I present evi dence that suggests that local bat distribution, diversity, and population size in managed forests are related to interspecific competition for limited roost sites, and to intraspecific division by sex that depends on local population numbers. INTRODUCT ION Findley (1993) summarized relationships between bat morphology, diet, and ecological niches to define a bat community in attribute space. Using work of Findley and Wilson (1982), Findley and Black (1983), and Aldridge and Rautenbach (1987), Findley st . . . it is possible to have a reasonable amount of confidence in the ability of morphology to provide an insight into the feeding and foraging of insectivorous bats. Bat reproduction, occurrence, and abundance are related to food abundance, and in that sense food is clearly a strong correlation between the diversity of physical structure and the diversity and richness of colonial bats. Perkins (1993) reported that the distribution of bat specie s in a neartic managed forest is not random, and speculated that forest bat distribution is a result of roost availability, insect concentrations, or competition between species resulting in displacement. Perkins and Peterson (1995) concluded that the dist ribution of reproductive female bats in a managed forest was affected by availability of roosts. In areas where harvest of large, older trees was highest, statistical analysis indicated a significant over representation of the largest bat species. In areas where timber harvest was non existent or minimal, the only competition exhibited at foraging sites was between the three species that forage exclusively or primarily on moths ( Corynorhinus townsendii , Myotis thysanodes , Myotis volans ). In contrast, Bell ( 1980) reported no foraging competition between paired bat species at concentrated insect patches in similar forested and Great Basin habitat. Here, I examine data regarding male and female distribution, prey, and roost selection in a managed forest. I hy pothesized that (1) the males forage separately from females of the same species; and (2) the determinant of the presence of any paired species at foraging sites is not solely foraging competition, but also involves roost availability. STUDY SITE My stu dy area is in northeastern Oregon on the Wallowa W; Figure 1). I sampled 140 sites distributed arbitrarily throughout four ranger districts: Hells Canyon National Recreation Area, Wallowa Va lley Ranger District, Eagle Cap Ranger District, and Pine Creek Ranger District. Over 486,000 ha (1.2 million acres) of public and private forest and canyons comprise the study area. Ponderosa pine ( Pinus ponderosa ), western larch ( Larix occidentalis ), Dou glas fir ( Pseudotsuga menziesii ), and white fir ( Abies grandis ) are the dominant tree species. I divided the study area into three habitat blocks, based on vegetation and management practices: Forest, Forest/Canyon Edge, and Canyon. Roost habitat surroundi ng Forest sample sites is limited to trees, snags, stumps, and a few buildings. This habitat comprises the largest area, had the most sample sites, and has had the greatest timber harvest in past decades. Roost habitat in the Forest/Canyon area included tr ees, snags, stumps, cliffs, talus, mines, and buildings. This was the second largest sample area, had fewer sample sites, and the least impact in terms of timber harvest. Canyon habitat is not considered in this analysis. I have recorded by capture or audi ble call signatures 13 species from the study area. Four of these species were not considered due to their low capture rates ( Lasiurus cinereus, Euderma maculatum, Corynorhinus townsendii , and Myotis yumanensis ). MATERIALS AND METHODS I sampled Forest a nd Forest/Canyon sites by setting mist nets over open water. Mist netting occurred from 1 June to 1 September 1984 1994. Netting periods lasted at least two hours after sunset. Bats were identified to


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 56 species, sexed, aged, weighed, and morphological measur ements were taken. To test for division of foraging sites by sex, I used the chi square test (Williams 1993). Lasionycteris noctivagans data are from Perkins and Cross (1992). To test for independence of distribution at foraging sites I paired each possi ble group of species and applied minimize this bias, I assigned a value for each species at each site as either present (1) or absent (0). RESULTS Chi square analysis of exclusivity in male and re productive female foraging patterns resulted in statistically significant separation between the sexes for all eight species for both portions of the study area, regardless of timber impacts (Table 1). However, ductive status is not considered, paired M. californicus, M. ciliolabrum , and M. thysanodes in both habitats had no foraging separation between the sexes. M. californicus, M. ciliolabrum , and M. thysanodes were the species that I captured the least of the eight considered. In the Forest/ Canyon habitat, M. evotis and M. lucifugus also had no significant segre gation by sex. If we divide the bats into morphological sizes based on forearm length, skull size, and mass, we get a large bat group ( E. fuscus, L. noctivagans ), a middle sized group ( M. evotis, M. volans, M. thysanodes ), and a small group ( M. lucifugus, M. ciliolabrum , and M. californicus ). The occurrence of large and small species together at sites was less than expected by chance in 67% (32 of 48) of the cases. Middle sized bats and small bats were less frequently associated than expected in 73% (35 of 48) of cases. M. evotis, M. thysanodes ) show competitive exclusion for both sexes. Forest and clearing ae rial insectivores ( E. fuscus, L. noctivagans, M. californicus, M. ciliolabrum , and M. volans ) produced mixed results indicating lower competition. In pairs of these species, 58% of cases indicated significant avoidance (29 of 50). M. lucifugus is the only water surface forager, but significantly avoided other species in 68% of cases (19 of 28). There was a slight difference in frequency of significant avoidance between the two habitats (when I excluded same species/different sex pairs). In the Forest habita t, competition was indicated in 70% of cases (74 of 105), while in the Forest/Canyon habitat competition occurred in 60% of cases (63 of 105). DISCUSSION My results indicate that the long held assumption that sexes forage in separate areas is valid, pa rticularly for the larger species, and those which form larger colonies outside of human structures. The lack of foraging habitat segregation by sex in the small and less numerous bat species ( M. californicus, M. ciliolabrum, M. lucifugus , and M. thysanode s ) suggests that prey biomass is not a critical factor in determining distribution or foraging sites when numbers of resident individuals are low. Analysis of species pairs by sex seems to validate the concept of competition for foraging areas as a factor influencing distribution (Findley 1993). If one takes into account prey species and foraging techniques, it is difficult to imagine how L. noctivagans or E. fuscus , who forage at tree top level at dusk, compete with M. lucifugus, M. californicus , or M. cil iolabrum , who forage low over meadows, water, in clearings, or under canopies in riparian zones. Whitaker et al. (1977) demonstrated that diets of M. californicus and M. lucifugus only overlap with the middle sized and large bat species in consumption of Diptera and Lepidoptera. M. lucifugus and M. californicus consume (by volume) mostly Diptera, while for large and middle sized bats, Diptera make up less than 10% of consumed volume. Lepidoptera seem to be the prey common to all bat species represented on the study area. Prey analysis indicates that the small bat species eat less Lepidoptera by volume by at least a factor of two when compared with the larger bat species. Dietary competition is most likely to occur in consumption of lepidopterans: L. noctiva gans (32% of prey volume), E. fuscus (21% of prey volume), M. evotis (46% of prey volume), M. thysanodes (46% of prey volume), and M. volans (78% of prey volume) (Whitaker et al. 1977; Whitaker et al. 1981). However, if prey competition is important, why i s there inconsistent evidence of foraging competition between E. fuscus and M. volans , and between L. noctivagans and M. volans ?


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 57 A close inspection of roosting behaviour provides the most likely answer. E. fuscus, L. noctivagans , and M. volans females a ll prefer abandoned woodpecker holes as maternity roosts, while males of these three species generally use crevices (Barclay 1985; Vonhof 1994; Kalcounis 1994; P. Ormsbee, pers. comm.). If roost availability is the determining factor in the significant dif ferences in paired bat distributions, then female L. noctivagans, E. fuscus , and M. volans should rarely occur together. Indeed, my data suggest that this is the case. Other bat species of both sexes seem to rely mostly on crevices in cliffs and trees, or exfoliating bark, in the absence of human structures (Perkins 1993; Kalcounis 1994; P. Ormsbee, pers. comm.). If we assume that roosts adequate for M. californicus are also adequate for other crevice species out compete the smaller and the less aggressive species. Differences in the distribution of bats between the two habitats in the study area can be attributed to the greater


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 58 harvest of trees in the Forest habitat. As well, in the Forest/Canyon habitat, alternate roost sites such as cliffs, caves, and human structures are more abundant than in the Forest habitat, thereby lessening competition. Perkins and Peterson (1995) noted potential foraging competition only among reproductive females of three bat species that are moth strategists ( M. thysanodes, M. volans , and C. townsendii ), and only in the Forest/Canyon habitat. Other significant differences noted in Tables 1 and 2 could be attributed to foraging inter actions, but results here, and those of Perkins (1993), Perkins and Peterson (1995), Humphrey (1975), and Bell (1980) all agree that bat distribution is more likely dependent upon roost availability and interspecific competition for roosts rather than diet ary competition. Sexual segregation in foraging areas occurs in most species, and may be correlated with local population densities of a given species IMPLICATIONS If competition for roosts and roost availability is important in determining the distribut ion and success of bat species in neartic forests, several questions arise: 1. Are present harvest practices especially harmful to smaller and less aggressive bat species? 2. Will future harvest practices result in lower population densities? 3. If com petition for roosts is reducing populations of small and less aggressive species in the summer, what are the effects for species that depend on forest tree roosts for hibernation? ACKNOWLEDGEMENTS I wish to thank the following individuals for their help in the field: Joshua Peterson, Andrew Perkins, B.J. Perkins, Travis Ash, Steve Farley, Holly Klocke, Paul Cryan, and Laurel Reuben. Monetary support was by various contracts with the Wallowa Whitman National Forest and the Oregon Department of Fish and Wi ldlife. I also wish to thank R. Anderson, S. Monnell, and K. for their encouragement and expedition of the projects. LITERATURE CITED Aldridge, H.D.J.N. and I.L Rautenbach. 1987. Morphology, echo location and resource partitioning in insectivorous bats . J. Anim. Ecol. 56:763 78. Barclay, R.M.R. 1985. Long versus short range foraging strategies of hoary ( Lasiurus cinereus ) and silver ha ired ( Lasionycteris noctivagans) bats and the consequences for prey selection. Can. J. Zool. 63:2507 15. Bell, G. 1980. Habitat use and response to patches of prey by desert insectivorous bats. Can. J. Zool . 58:1876 83. Findley, J. 1993. Bats a community perspective . Cambridge Univ. Press, Cambridge, U.K. Findley, J. and H.L. Black. 1983. Morphological and dietary structuring of a Zambian insectivorous bat community. Ecology 64:625 30. Findley, J. and D. Wilson. 1982. Ecological significance of chiropteran morphology. In Ecology of Bats , T.H. Kunz (editor), pp. 24 3 50. Plenum, New York, N.Y. Humphrey, S.R. 1975. Nursery roosts and community diversity of Nearctic bats. J. Mammal . 56:321 46. Kalcounis, M. 1994. Selection of tree roost sites by big brown ( Eptesicus fuscus ), little brown ( Myotis lucifugus ) and hoary ( Lasiurus cinereus ) bats in Cypress Hills, Saskatchewan. Paper presented to the 24th Ann. North American symposium on bat research, Ixtapa, Mexico. Perkins, J.M. 1993. Are bats normal? Paper presented to the 23rd North American symposium on bat research, Gainseville, Fla. Perkins, J.M. and S.R. Cross. 1992. Sexual differentiation in migratory patterns of Lasionycteris noctivagans in Oregon and Washington. Paper presented to the 22nd North American symposium on bat research, Austin, Texas. Perkins, J.M. a nd J.R. Peterson. 1995. Distribution of foraging female bats in a managed forest. Paper presented to the 2nd National Wildlife Conference, Portland, Oreg. Vonhof, M.J. 1994. Roosting ecology and roost site selection by forest dwelling bats in the West Arm Demonstration Forest near Nelson, B.C. Paper presented to the 24th North American symposium on bat research, Ixtapa, Mexico. Whitaker, J.O., Jr., C. Maser, and L.E. Keller. 1977. Food habits of bats of western Oregon. NW Science 51:46 55. Whitaker, J.O. , Jr., C. Maser, and S.P. Cross. 1981. Foods of Oregon Silver Haired Bats, Lasionycteris noctivagans . NW Science 55:75 77. Williams, B. 1993. Biostatistics: concepts and applications for biologists . Chapman and Hall, N.Y.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 59 FIGURE 1 . Study area, WWNF, Oregon, U.S.A. Thin line indicates forest boundary. East of the broken line is the HCNRA. Small dots represent single sample sites to nearest section. Large dots show two sites within section.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 60 Potential Effects of Livest ock Water Trough Modifications on Bats in Northern Arizona Stuart R. Tuttle , Department of Biological Sciences, Northern Arizona University, Flagstaff, AZ 86011, USA Carol L. Chambers , School of Forestry, Northern Arizona University, Flagstaff, AZ 86011, U SA Tad C. Theimer , Department of Biological Sciences, Northern Arizona University, Flagstaff AZ 86011, USA WILDLIFE SOCIETY BULLETIN 34(3): 602 608; 2006 Abstract In the southwestern United States, livestock water troughs may be the only water source av ailable to bats during dry seasons or periods of drought. We found that 38% of the 90 livestock water troughs we surveyed in northern Arizona, USA, were modified with either fencing to separate pastures or braces to strengthen the structures. We tested if these modifications could affect bat drinking behavior or increase injury risk by simultaneously videotaping modified and unmodified troughs in a series of crossover experiments performed between 1 March and 26 August 2004. The bats that we observed did no t avoid modified troughs but required 3 6 times the number of passes to approach the water surface at both troughs with fences and those with support braces. The number of passes required to drink increased with reduced water surface area, suggesting that modifications of smaller troughs may have a greater effect. Small (e.g., Myotis spp.) and large (e.g., pallid bat [ Antrozous pallidus ]) bats responded similarly in the experiments. These effects may be energetically expensive for bats, especially during pe riods of high energy demands, such as pregnancy and lactation. Although we did not document any injuries or mortalities, 16 bats contacted wires at modified troughs with smaller surface area. This suggests that modifications of smaller troughs may pose hig her risks of injury. To reduce these risks, we recommend removing modifications on water troughs whenever feasible. Key words Antrozous pallidus , Arizona, energetic costs, fences, flight path, Myotis , pallid bat. Estimates of daily evaporative water loss in bats range as high as 30 1971, Webb et al.1995) and for big brown bats ( Eptesicus fuscus ) estimates of the percentage of total dietary water obtained from free water sources range from ~22% (Kurta et al. 1 990) to 42% (Carpenter 1969), indicating at least some reliance on free water. Bats drink water by swooping over a water source and lapping at the surface (Harvey et al. 1999), but it is unknown how critical free water is for bat survival. Several studies demonstrated that diurnal roost sites tend to be closer to water sources than expected based on random locations, and foraging activity has been shown to be higher near water sources than farther away (Rabe et al. 1998, Waldien and Hayes 2001). Both relati onships could be due to either dependence on free water or the greater prey abundance associated with water sources (Entwhistle et al. 1997, Rabe et al. 1998, Evelyn et al. 2004, but see Waldien et al. 2000). Bats can potentially obtain water from natura l sources that provide an open, unobstructed surface. In arid regions like the southwestern United States, artificial water sources may be the only water available, especially during periods of drought. In these areas, livestock water troughs (hereafter r eferred to as troughs) supplied by a permanent water development such as a well or spring, may be the most reliable year round water source for bats. However, modifying troughs by placing wires, braces, or other structures above the water may either preven t access or require bats to make multiple approaches to access water. Troughs are modified in these ways to allow livestock access to Figure 1 . Experimenta l tr o ugh design at Raymond Wildlife Area, Arizona, USA, showing a modified circular and an unmod ified rectangular trough (1 July 2004). Black and white video cameras and infrared lights are mounted on the pole between the troughs. The recording equipment is l ocated 76m away from the trough s.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 61 water from 2 or more pastures, to prevent livestock from entering the trough, or to maintain trough stability. Andrew et al. (2001) speculated that trough modifications design, or water level could increase bat mortality. Bats not dying immediately from an impact with a modification or interior side of a trough may drown if an escape structure is not present that allows the m to climb out of the water (Kolb 1984). Although it is unknown how many troughs exist in the southwest, some estimates have been in the tens of thousands (D. Taylor, Bat Conservation International, personal communication). The Natural Resources Conservat ion Service (NRCS) documented the installation of 180 water facilities from 1997 2005 on non federal lands in 5 counties of northern Arizona, with 500 more planned for the same area by 2010 (NRCS, unpublished data).Given this potential for bat trough inter actions, it is important to understand how trough modifications may affect bat use and if they increase risk of mortality. To conduct this study we surveyed troughs in northern Arizona to determine the most common types of trough configurations and modifi cations present. We used this information to design and implement a series of experiments to determine if the most common modifications affected bats. Specifically, we were interested in learning: 1) do fences across troughs alter access of bats to the wat er surface?, 2) does decreasing the water surface area affect bat behavior at fenced troughs?, 3) do support braces on rectangular troughs reduce access to water?, and 4) what is the potential for trough modifications to cause bat injury or mortality? Our methods did not allow us to identify bat species in these experiments, but we were able to determine if larger bats (e.g., those similar in size to the pallid bat [ Antrozous pallidus ], ~30g) responded differently than smaller bats (those similar in size to Myotis spp., ~6 8 g). Study Area Between 1 March and 19 May 2004, we conducted an inventory of livestock water troughs across northern Arizona on federal and state land and on private land when granted permission. Between 20 May and 26 August 2004, we co nducted 4 experiments on the 6,070 Ranch Wildlife Area approximately 60 km southeast of Flagstaff, Arizona, USA. The study site was located at 1,731 m elevation on the eastern edge of the wildlife area in Great Basin grassland (Brown 1994) consisting primarily of blue grama ( Bouteloua gracilis ), galleta ( Pleuraphis jamesii ), four wing saltbush ( Atriplex canescens ), and snakeweed ( Gutierrezia sarothrae ). Two livestock tanks (ponds) were located 3 km from the stud y site and contained water until 1 June 2004. Other tanks and troughs were >6 km from the study site. In addition to the experiments on the Raymond Wildlife Area, we conducted single night experiments at 2 other sites, House Rock Wildlife Area (hereafter House Rock) on the north rim of the Grand Canyon (also managed by the Arizona Game and Fish Department) and at another site 19 km north of House Rock on Bureau of Land Management (BLM) land. Both sites were ~1,700 m elevation in Great Basin grassland with similar plant communities to Raymond. Additional water sources were located approximately 3 km away from each study site. Methods Trough Inventory We collected data whenever we encountered troughs along public roads across northern Arizona and on 4 ranche s in grassland, desert scrub, and pinyon juniper woodland ( Pinus edulis Juniperus osteosperma ) vegetation types from ~1,400 m to ~1,800 melevation. For each trough we measured dimensions (height, diameter for round, or width and length for rectangular trou ghs) and recorded whether modificat ions were spanning the surface of the water that connected 2 sides could reduce access to the water surface such as wooden boards or tires). We also noted presence of escape structures, presence of animal carcasses, and distance from top of trough to the water surface (water level). Escape s tructures were any object placed in the water that could allow wildlife to escape, including floating boards or logs, as well as intentionally constructed ramps of metal, wire or rocks. We did not search the sediments on the bottom of troughs for animal re mains but noted any animal carcasses floating in the water or on the surface of the sediment. Trough Experiments We conducted 4 experiments (3 on rectangular and 1 on circular troughs) at the Raymond Wildlife Area to determine how trough modifications aff ected bat use by simultaneously comparing use at an experimental


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 62 (modified) trough and a control (unmodified) trough. The 2 rectangular troughs (spaced 100 m apart) had been present at the site with continuous water supply for .2 years. The water surface a rea of each trough was 7.5 m 2 compared to the mean of 4.3 m 2 (SE 1/4 0.4, n 1/4 38) for rectangular troughs in the survey. We placed the 2 circular troughs (also spaced 100 m apart) at the site for this study. They each had a surface area of 4.7 m 2 compare d to the mean of 10.5 m 2 (SE 1/4 2.1, n 1/4 52) for circular troughs in the survey. We selected the most common types of modifications, as determined by our survey, to use in our experiments. To reduce confounding effects of trough location, midway throug h each experiment, we switched the modification to the alternate trough in a crossover design (Dean and Voss 1999). Thus, each trough acted as both the control and the experimental unit in each experiment. Throughout all experiments, we maintained the wate r level in each trough at 13 cm below the rim, corresponding to the mean water level in the trough inventory. We simultaneously filmed bat activity at both troughs for 8 hours per night using a black and white Video, Burbank, California) mounted 2 m high on a pole 4 m from each trough (Fig. 1). We used infrared illumination (HTI 790, 850 nm, Technology Express, Glendale, Arizona) for each camera. A 12 V videocassette recorder ( JPI 12VCR, JP Industries, San Jos e, California) and video splitter ( JPI BQ4, JP Industries) located 76 m from each camera in a protected location simultaneously recorded the 2 camera images on 1 videotape. At House Rock, we conducted a single night (80 min) experiment filming simultaneou sly on 2 rectangular troughs (spaced 100 m apart); at the BLM site, we conducted a single (80 min) experiment on 1 circular trough (described below). All troughs had been present on site with continuous water supply for >1 year. For each experiment, we as ked 2 questions: 1) was the number of approaches at modified and unmodified troughs the same (e.g., did bats avoid modified troughs?), and 2) was the flight behavior at modified and unmodified troughs the same? We defined an approach as any time a bat ente red the camera field of view and then left. The number of individuals could not be determined because we were unable to distinguish whether approaches represented separate bats or returns by the same individual. We categorized flight bats were close enough to the water surface to potentially drink). In addition, when a bat approached a modification we recorded whether it avoided (altered fligh t path to avoid the modification), passed through (flew between the wires of the modification), made contact (touched the modification and either flew away or fell into the water), or did not interact with the modification (flight was parallel to the modif ication or no alteration in flight path detected). Experiment 1A . B at access to the water surface. At the Raymond site, we replicated the typical fence found in the trough inventory by placing a 3 strand barbed wire fence across the center of a rectangula r trough. The first strand was 12 cm above the trough rim, the second strand 30 cm above the first, and the top strand 30 cm above the second. We left the other trough unmodified as the control. We filmed both troughs for 5 nights and then switched the fen ce to the control trough and filmed for 5 more nights from 20 29 May. At the House Rock location, we conducted a single night experiment on 3 August 2004 to test the results of experiment 1A at a different location. The rectangular troughs were similar to those at the Raymond site. We placed a 3 wire fence across both troughs, filmed simultaneously for 20 minutes, then removed the fence for 20 minutes and repeated this sequence once. Experiment 1B . Do fences across circular troughs alter b at access to the water surface? At the Raymond site, we covered the rectangular troughs and placed 2 2.4 m diameter circular troughs 100 m apart in the same area. We placed 3 strands of barbed wire across one trough as in Experiment 1A. After 3 nights we switched the fenc e to the control trough and filmed for 2 more nights from 4 8 July. The following night (9 Jul) marked the beginning of the summer monsoons in this area, after which water was widely available. Bat use of troughs dropped and we discontinued experiments at this site. At the BLM site, we conducted a single night experiment on 26 August to test the results of experiment 1B at a different location. We placed fencing over the water of one 2.4 m diameter circular trough for 20 minutes, then removed it for 20 minu tes, and repeated the sequence once. Experiment 2 : How does decreasing the water surface area affect bat access at fenced rectangular troughs? In


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 63 this experiment, we placed the same 3 strand fence across both rectangular troughs at Raymond and then reduce d the water surface area of one trough by placing plywood boards over half of the water at each end of the trough, effectively reducing the trough length by 50%. After filming bat approaches for 5 nights, we switched the plywood to the control trough and f ilmed for another 5 nights, from 15 24 June. Experiment 3 : Do support braces across na rrow troughs affect bat access? At the Raymond site, we simulated a long, narrow trough by covering one half of each rectangular trough used in previous experiments with a tarp until they had the same average dimensions (0.76 m 3 4.45 m) as found in the trough survey. We then placed 3 boards (2 cm 3 4 cm3 75 cm) at 110 cm intervals across one trough to simulate support braces and left the other trough open as a control. We filmed for 4 nights and then switched the boards, filming for 4 more nights from 26 June 3 July. Mist netting for video comparison . After completing trough experiments, we simultaneously mist netted and videotaped bats over circular and rectangular tr oughs at each site to relate video images of bat approaches to the experimental troughs to the species captured in mist nets. We captured bats using 38 mm mesh 2.6 m 3 6 m mist nets (Avinet CH2, Avinet, Inc., Dryden, New York) placed across each trough. W e opened the nets at sunset and monitored continuously until either sunrise or midnight, depending on bat activity at troughs. We identified captured bats to species, determined reproductive status and then released them. We captured and handled animals un der guidelines of the American Society of Mammalogists and with approval of Northern Arizona University Institutional Animal Care and Use Committee (IACUC Protocol 04 006) and Arizona State Game and Fish research permit number SP747870. Statistical analys es : To determine whether modifications caused bats to shift their use to unmodified control troughs, for each experiment we tested whether the total number of approaches at modified and unmodified troughs differed using chi square analysis (Sokol and Rohlf 1995). We tested whether modifications altered the ability of bats to access the water surface in 2 ways. First, we compared the number of surface and above approaches at modified and unmodified troughs using chi square contingency table analysis for each experiment separately. We then analyzed video sequences in more detail by categorizing bat behavior as when successive approaches by a bat were separated by ,1 minute across all experiments. We then compared: 1) the number of single approaches at modified and unmodified troughs that successfully reached the surface, 2) the number of multiple approaches that eventually resulted in reaching the surf ace at modified versus unmodified troughs, and 3) the number of approaches in a multiple approach sequence required before reaching the surface at modified and unmodified troughs. Results Trough Inventory For the 90 troughs we measured, 58% were circular, 42% were rectangular, and the most common modifications were fences across both rectangular (18.4%) and circular (30.8%) troughs and braces across rectangular troughs (26.3%). Circular troughs had nearly 3 times the mean water surface area (12.04 m 2 , SE1/ 42.09, n 1/4 52) compared to rectangular troughs (4.26 m 2 , SE1/4 0.44, n 1/4 38). Twelve percent of surveyed troughs were located in pinyon juniper woodland; 88% were in grasslands or desert scrub similar to the experimental sites. Only 8% of rectangular a nd 6% of circular troughs included a structure for wildlife to escape from the water. Although we found no bat carcasses floating in any of the troughs, we did not search the sediments for remains. Bats killed and floating in a trough likely would sink to the bottom if not scavenged. Mist Netting We captured 31 bats representing 6 species: long legged myotis ( Myotis volans ; 1 juvenile female), fringed myotis ( M. thysanodes ; 1 adult male, 1 adult female), western small footed bat ( M. ciliolabrum; 1 adult ma le, 1 adult female), California myotis ( M. californicus ; 2 adult females), western pipistrelle ( Pipistrellus hesperus ; 4 adult males, 6 adult females, 2 juvenile females) and pallid bat (2 adult males, 9 adult females, 1 juvenile female). Two Myotis spp. e scaped from the net before identification. One male was scrotal and 11 females appeared to be post lactation; no others were in obvious reproductive condition, most likely because netting occurred late in the summer. When independent observers viewed the v ideotapes, captured bats classified as small were western pipistrelle and Myotis spp., and those classified as large were pallid bats. Trough Experiments For all experiments combined, we recorded 2,049 total


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 64 approaches at modified troughs by bats, classif ying 12% as non interaction. Of the 1,825 interactions, 95% avoided the modification by altering their flight path. Bats used 908 (53%) or 1808 turns (27%) to avoid the fence or bars, adjusted their flight path by flying vertically out of the camera view ( 8%), or avoided the modification by curving their flight over the wires (12%). In 3.6% (65) of approaches at modified troughs, bats passed through the modification, and in 1.3% (23), they made contact with the modification. Sixteen of the 23 contacts were with wires at troughs with reduced water surface area (exp. 2), a rate of 3.2% of approaches, and 14 of these were large bats. No bats fell into the water and all flew out of the viewing frame after contact but, otherwise, it was impossible to assess wheth er bats were injured because of contact. When either rectangular or circular troughs were modified by placing 3 strands of barbed wire across the surface, the percentage of approaches at or near the water surface was roughly one half or less of that at un modified troughs (Table 1) in all experiments. In contrast, although the number of approaches recorded at fenced troughs was 37% higher than unmodified troughs, in 2 of the 6 experiments we recorded more approaches at modified troughs; while in the other 4 experiments, we recorded more approaches at the modified trough (Table 1). In all of the experiments, we found no difference in the response of bats classified as large versus those classified as small (P1/40.14, 0.47, and 0.26 for Raymond exp. 1A, 1B, an d 2, respectively). When we simulated braces across a narrow rectangular trough, we found the total number of approaches was higher at modified troughs, while the percentage of approaches at or near the water surface was roughly 25% of that at unmodified troughs (Table 1). Again, we detected no difference in responses of large versus small bats in their response to modification (P 1/4 0.23). When approaches across all experiments at Raymond proaches separated in time by .1 min) b y 1 min), we found that the percentage of single approaches at or near the water surface was 3 times higher at unmodified troughs compared to modified troughs ( 71% vs. 25%; v 2 1 1/4 20.2, P _ 0.001). Likewise, in sequences in which bats approached troughs multiple times in rapid succe they never reached the surface in 39% of the cases at modified troughs compared to 3% at unmodified troughs (v 2 1 1/444.1, P _ 0.001). In these multiple approach sequences, the mean number of approaches required before a successful approach at the water surface was 1.8 (SE 1/4 0.29) at modified troughs compared to 0.3 (SE 1/4 0.07) at unmodified troughs (Z 1 1/4 5.25, P, 0.001). Discussion Our results suggest that trough modifications altered the behavior of bats approaching modified troughs in all experiments. The most common effect was the decreased percentage of approaches at the water surface, suggest ing that bats approaching modified troughs expended more effort and flight time to obtain a drink. This was supported in our analyses that divided approaches into those occurring in rapid succession (multiple approach sequences) and those that were separat ed from other approaches by .1 minute (single approaches). Bats made 3 times more single approaches and 6 times more approaches in multiple approach sequences over modified troughs before they successfully reached the water surface. In addition, bats were 10 times more likely to make multiple approaches without accessing the water surface at modified troughs than at unmodified troughs. Although the duration of the experiment at the 2 additional sites (House Rock and BLM) was shorter, the results were simila r, with a 2 fold higher success rate at reaching the surface at unmodified troughs versus modified troughs. In addition to an increased number of approaches to access the water surface, in all experiments, flight paths were often altered at modified trough s, requiring sharp turns rather than a smooth, arcing swoop over the water. The timing of these experiments corresponded to the most energetically demanding time for most southwestern bat species because of pregnancy and Kurta et al. 1990). The mean daily energy requirement of lactation is twice that of pregnancy and 3 times that of non reproductive periods (Kurta et al. 1990). To avoid negatively affecting bats during our experiments, we did not mist net until late in the season. As a result, most of the bats we handled were not in reproductive condition. However, given that adult females commonly were captured in our mist netting sessions, it is likely that they were using these troughs earlier in the season (Rabe 1999, C . L. Chambers, Northern Arizona University, unpublished data). As a result, the flight modifications and the need to make multiple approaches to drink successfully at modified troughs could increase energetic demands during a critical period of the reprodu ctive cycle.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 65 One potential criticism of our experimental design was that it lacked the washout period often included in crossover designs to account for any residual effects of the experimental manipulation after it had been switched or removed (Dean and Voss 1999). If residual effects occurred, we should have detected a shift in behavior from the first night after moving the modification compared to later nights at Raymond Ranch, a shift that was not evident in visual inspection of our data. Likewise, if strong residual effects were present, they should have reduced our power to detect differences between modified and unmodified troughs in the very short duration experiments at House Rock and BLM, in which modifications were shifted every 20 minutes. Resid ual effects in this case should have made it impossible to detect differences among treatments, when in fact we found significant effects. These results indicated that bats responded almost immediately to the presence or absence of modifications. In additi on, the greater abundance of bats at our House Rock and BLM sites yielded total numbers of approaches in a single night that approximated those across several nights at Raymond Ranch; thus, sample sizes for tests in both experiments were similar, in spite of differences in experiment duration. One aspect that we did not address was whether bats adapt their behavior to modifications over time, and the negative responses we documented, therefore, would decrease as bats became familiar with the presence of mo difications. However, at least over the relatively short term of our experiments, bats did not increase surface approaches over time at modified troughs, as would be expected if adaptation over time were occurring. Even if resident bats could potentially a dapt to trough modifications through time, modifications for migratory bats would be novel encounters at each stopover site. Overall, we found no evidence that large and small bats responded differently to modifications. However, size alone may not be a g ood predictor of flight performance because of the variability in aspect ratio and wing loading across species. A major limitation of our video method was that the resolution was not great enough to allow for species identification, although we could disti nguish large from small bats. Simultaneously recording bats while mist netting allowed us to assign some species to each size category, but we did not capture all species documented to occur in the area in previous studies (Hoffmeister 1986, Rabe 1999, C. L. Chambers, unpublished data). The large bats we observed in our experiments likely were pallid bats, a maneuverable bat with low wing loading despite weighing 3 4 times that of small bats (Harvey et al. 1999). Although we did not capture the intermediat e sized Mexican free tailed bat ( Tadarida brasiliensis [11 15 g]) or big brown bat (14 21 g), both have higher wing loading than pallid bats (Harvey et al. 1999) and may be more negatively affected by trough modifications. Determining species specific resp onses to modifications remains an important challenge for future studies. Only 1.3% of 1,825 bat approaches resulted in contact with a modification and, in all cases, no bats struck the modification in such a way to knock them into the water. However, mos t of these occurred at smaller surface area troughs, where collisions averaged 1.6 per night. We believe these observations indicate increased potential for mortality or injury, with the risk being higher at smaller troughs. In this respect, modification o f rectangular troughs may be more likely to result in negative effects on bats for 2 reasons. First, the mean water surface area of rectangular troughs in our survey was much smaller than that of circular troughs. Second, when a single fence or support bra ce is placed across a circular trough, the length of the longest potential flight path is not reduced if bats fly parallel to the modification. This is not true for modifications across rectangular troughs. During our mist netting, we observed 3 bats that fell from nets into the water. In 2 cases bats swam to the edge of the trough and escaped either by using a rock ramp or by climbing up the rough inner wall of the trough. Given that many troughs in our survey were smooth walled steel and did not contain an escape structure, we believe bats falling into these troughs may less easily escape. Although one bat in our experiments was able to launch into flight from the water surface, injury, hypothermia or exhaustion may prevent a bat from achieving flight in the absence of a means to exit the water. One rancher reported f inding several dead bats in a 2 m diameter circular trough with no modifications but with a water level maintained .20 cm below the rim (D. Carroll, private rancher, personal communication). I n this case, bats may have collided with the vertical wall above the water while attempting to drink or forage at the surface. Of the troughs in ou r survey, 38% had water levels 10 cm below the rim (and as much as 26 cm).


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 66 Allowing water levels to fall well below the rim also effectively reduces the water surface area available to bats due to the angle of approach necessary to avoid the trough wall and still access the water surface. Given the strong effect of reducing surface area on the number of collision s we documented in this study, we believe low water levels combined with trough modifications could increase the potential for bat mortality. The majority of bats did not make contact with or fly between fence wires or under bars. Instead, changes in thei r flight path allowed bats to avoid the modification using primarily 908 and 1808 turns. Experimental modifications were limited to 3 strands of standard diameter barbed wire and wooden bars across the water surface. Modifications with greater complexity o r smaller diameter wire potentially could act as a greater threat. Indeed, if wires were thin enough and spaced more closely together, fence modifications could resemble the harp traps commonly used to capture bats. Management Implications Our data demons trate that trough modifications may reduce the ability of bats to access the water surface and, thereby, potentially increase the energetic costs of drinking. We documented no mortality due to modifications during our study, and overall rate of collision w ith modifications was very low, suggesting that trough modifications we studied may not need to be mitigated. However, we argue caution be exercised in future modifications for several reasons. First, although all bats that collided with modifications wer e able to fly away, we were unable to assess whether contact resulted in injury. Second, even though the overall rate of collision was low, most of these occurred at troughs with smaller surface area, where collisions averaged 1.6 per night. Third, most of these collisions were large bodied bats, suggesting that the effects of modifications may differentially affect some species over others. Fourth, our inability to determine bat species on our videotapes leaves open the possibility that some large bodied, less maneuverable species are excluded from modified tanks. As a result, we recommend that modifications be removed or altered, especially for small troughs, so they do not span the entire water surface. In many cases this can be achieved relatively easily and inexpensively (e.g., for narrow troughs that need additional support for the sidewalls, trough supports can be placed on the outside of the trough rather than across the water surface). For troughs that retain modifications, adding an escape structure of rock, wood, or metal on the inside edge would allow bats to crawl out of the water and would be relatively easy and inexpensive. For smaller troughs with reduced surface area, a separate trough could be installed for each pasture. A second trough will cost less than $1,000 depending on size and type selected, may be cost shared through government conservation programs on private land, and would have the added benefit of reducing soil compaction and erosion. Finally, adjusting float valves to maintain t he water level at or near the trough rim provides maximum water surface area and minimizes the risk of collisions with the trough wall. Acknowledgments This study was funded by a grant from the Wildlife Habitat Management Institute of the Natural Resource s Conservation Service and a student scholarship from Bat Conservation International. We sincerely thank D. Belitsky, manager of the Raymond Wildlife Area, and M. Brown, manager of the House Rock Wildlife Area for support, and the Arizona Game and Fish Dep artment for permission to film troughs on the wildlife areas. J. Gagnon provided video design and equipment suggestions. We thank D. Kuhns for help in the field, C. Calvo, D. Pokrajac, M. Evans, C. Boone, and S. Penrod for assistance with the laborious tas k of viewing and analyzing videotapes. We thank 2 anonymous reviewers for their comments that greatly improved themanuscript. Literature Cited Andrew, N. G., V. Bleich, A. Morrison, L. Lesicka, and P. Cooley. 2001. Wildlife mortalities associated with art ificial water sources. Wildlife Society Bulletin 29:275 280. Brown, D. E. 1994. Biotic communities: southwestern United States and northwestern Mexico. University of Utah, Salt Lake City, USA. Carpenter, R. E. 1969. Structure and function of the kidney and water balance of desert bats. Physiological Zoology 42:288 302. Dean, A., and D. Voss. 1999. Design and analysis of experiments. Springer Verlag, New York, New York, USA. Entwhistle, A. C., P. A. Racey, and J. R. Speakman. 1997. Roost selection by the br own long eared bat Plecotus auritus. Journal of Applied Ecology 34: 399 408. Evelyn, M. J., D. A. Stiles, and R. A. Young. 2004. Conservation of bats in suburban landscapes: roost selection by Myotis yumanensis in a residential area in California. Biologic al Conservation 115:463 473. Harvey, M. J., J. S. Altenbach, and T. L. Best. 1999. Bats of the United States. Arkansas Game and Fish Commission, Little Rock, USA. Hoffmeister, D. F. 1986. The mammals of Arizona. University of Arizona, Tucson, USA. Kolb, A. 1984. Schwimmen, starten vom wasser und orientierung einheimischer fledermaeuse. Zeitschrift Fur Saugetierkunde 49:1 6. [In German.] Kurta, A., T. H. Kunz, and K. A. Nagy. 1990. Energetics and water flux of freeranging big brown bats (Eptesicus fuscus) du ring pregnancy and lactation. Journal of Mammalogy 71:59 65. and water requirements of captive Myotis thysanodes and Myotis


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 67 lucifugus (Chiroptera). Comparative Biochemical Physiolog y 39:549 552. Rabe, M. J. 1999. Bat habitat use in pinyon juniper woodland and grassland habitats in northern Arizona. Thesis, Northern Arizona University, Flagstaff, USA. Rabe, M. J., T. E. Morrell, H. Green, J. O. deVos, and R. Miller. 1998. Characterist ics of ponderosa pine snag roosts used by reproductive bats in northern Arizona. Journal of Wildlife Management 62:612 622. Sokol, R. R., and F. J. Rohlf. 1995. Biometry: the principles and practice of statistics in biological research. Third edition. W. H . Freeman, New York, New York, USA. Waldien, D., and J. P. Hayes. 2001. Activity areas of female long eared Myotis in coniferous forests in western Oregon. Northwest Science 75:307 314. Waldien, D., J. Hayes, and E. Arnett. 2000. Day roosts of female long eared Myotis in Western Oregon. Journal of Wildlife Management 64:785 796. Webb, P. I., J. R. Speakman, and P. A. Racey. 1995. Evaporative water loss in two sympatric species of vespertilionid bat, Plecotus auritus and Myotis daubentoni: relation to forag ing mode and implications for roost site selection. Journal of Zoology, London 235:269 278. Stuart R. (Stu) Tuttle (photo) is a Wildlife Biologist with the Natural Resources Conservation Service in Flagstaff, Arizona. He recently completed gree at Northern Arizona University. He received his B.S. in Vocational Agriculture form Colorado State University. He served as Secretary and is now President elect for the Arizona Chapter of The Wildlife Society and Program Committee Chair for the 2007 W ildlife Society Conference in Tucson. His professional interests are in habitat restoration and wildlife livestock interaction. At home, he and his wife, Mary, enjoy competing in dog agility. Carol L. Chambers is an Associate Professor of Wildlife Ecology with the School of Forestry at Northern Arizona University. She worked as a Faculty Research Assistant at Oregon State University while completing her Ph.D. in Wildlife Sciences. She received her M.S. in Forestry Tuttle et and B.S. in Biology from the Univ ersity of Kentucky. She has been a board member, web site manager, and is currently President for the Arizona Chapter of The Wildlife Society. She has been a member of national and local chapters of TWS since 1992. Her research is focused on wildlife habit at relationships. Tad C. Theimer, an associate professor in the Department of Biological Sciences at Northern Arizona University, received his B.S. in biology from University of the Pacific, his M.S. in zoology from Colorado State University, and his Ph.D. in zoology from Northern Arizona University. A past president of the Arizona Chapter of The Wildlife Society, his research interests are in bird and mammal ecology. Special Section Associate Editor: Krausman. Table 1. Total number of approaches and pe rcentage of approaches that were at or near the water surface by bats at modified (Mod) and unmodified (Unmod) water troughs in experiments conducted in northern Arizona, USA, 20 May 26 August 2004. Total no. of approaches % surface approaches Exp ./trough type Site a Modification Mod Unmod x 2 (df=1) P Mod Unmod x 2 (df=1) P 1A Rectangular Ray Fence 682 468 39.8 <0.001 41 84 208.4 <0.001 1A Rectangular HR Fence 141 230 21.4 <0.001 34 66 35.1 <0.001 1B Circular Ray Fence 26 96 40.2 <0.001 23 73 21.6 <0.001 1B Circular BLM Fence 544 329 53.0 <0.001 20 50 84.4 <0.001 2 Rectangular Ray Fence/area 516 305 54.2 <0.001 34 86 145.6 <0.001 3 Rectangular Ray Braces 140 95 8.6 <0.001 16 69 69.8 <0.001 a Ray = Raymond Wildlife Area; HR = House Rock Wildlife Area; BLM = Bureau of Land Management locations.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 68 Cave Conservation: Special Problems of Bats by Gary F. McCracken NSS Bulletin 51: 49 51. (June 1989). Ignorance as to the real status of populations of almost all bat species is a major problem for their conservation. This ignorance is reflected in the IUCN minimalist and biased. The recent proposition that we secure, rather than re d lists, is extended to bats. Available information regarding the status of the five species of North American bats listed as endangered is reviewed, and these species are used to illustrate major problems encountered by bat populations. All of these speci es rely on cave roosts. Their habit of roosting in large aggregations during hibernation and/or reproduction make these and other cave dwelling bats particularly vulnerable to disturbances which can reduce populations. Types of disturbances and their likel y effects are discussed. The long life spans and low reproductive rates of bats mandate that they will recover slowly following population reductions. Habitat alteration and destruction outside of roosts and poisoning from pesticides also have impacted neg atively on bat populations; however, roost site disturbance and habitat destruction have probably had much greater negative effects than has pesticide poisoning. Because disturbance within their cave roosts is a major problem in bat conservation, construct avoided) is encouraged. Criteria for constructing these lists of caves are discussed. Red Books, Green Lists, And a Lack of Information Each year the Internationa l Union for the Conservation of Nature (IUCN) updates the Red Data Book which lists plant and animal species known to be endangered, vulnerable, or rare. The 1988 Red Data Book places 33 bat species in these categories. As there are approximately 900 speci es of bats in the world (nearly one fourth of all mammal species), this number should lead anyone with even remote awareness of the worldwide extincti on crisis to question whether this list reflects reality with regard to bat species that are threatened. In reality, the red list does not come close to giving an accurate picture of the problem. First, consider that the red list has a substantial geograph ical bias toward North American species. The standard reference on North America bats (Barbour and Davis, 1969) lists 39 species of bats in North America, north of Mexico. These 39 species comprise about 5% of the worldwide bat species diversity. However, of the 33 threatened bat species on the IUCN list, 5 are native to North America. So, a fauna comprising 5% of total bat species diversity, accounts for 15% of the species considered as threatened. I argue that this bias does not reflect reality with regar d to species endangerment. Rather, this bias reflects our ignorance regarding the status of most bat populations. We simply know the status of bats in North America better than for most other parts of the world. I also argue that our degree of ignorance is even more frightening when you recognize that we are not even certain how accurate the IUCN red list is for bat species in North America. This is so because for most bat species in North America, much less for those elsewhere (particularly in the tropics) , we simply do not have the information to determine whether overall population sizes are stable, decreasing, or if they are decreasing, at what rates? So our ignorance on the status of bats is extreme. Given this ignorance, the IUCN red list gives a highl y inaccurate and minimal assessment of our current extinction crisis. Recognizing this, prominent conservation biologists recently have suggested that the construction of red lists has been a major tactical error by those who wish to biota (Imboden, 1987; Diamond, 1988). Red lists are thought to be a tactical error because the existence of such a list may lead to the assumption that if a species is not on the list that species is not in jeopardy. This, of course, is not how the list sh ould be interpreted. Many species that are not on the list should be, but are not, correct this tactical error, it has been suggested that rather list secure. To be on the green list a species should meet the 1988). With a green list, it is a rgued, the burden of proof is shifted to those who wish to maintain that all is well with a species. Those proposing green lists have been concerned with birds, not with bats. Certainly, much more is known about


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 69 the status of birds than of bats. However, i t is species would qualify for inclusion on a green list. This being the case with birds, I also suspect that qualify for such a list. Some Things That We Do Know With our ignorance as a perspective, I wish to consider some of what we do know about the status of bats, particularly cave bats. This requires going back to the red list. Of the 39 bat species in North America, north of Mexico, 18 rely substantial ly on caves for roosting sites. Some of the remaining 21 species also are occasionally found in caves, but caves evidently are not absolutely essential to them. Of the 18 species for which caves are essential, 13 species utilize caves year round; both for reproduction and as winter roosts. The remaining 5 species rely on caves as hibernating sites, but roost elsewhere during reproduction. Four of the 5 North American species on the red list require caves year round (Table 1), and one species (the Indiana ba t) requires caves for hibernation, but roosts elsewhere during the summer. So all North American bats listed as threatened are cave dwelling; there appears to be a correlation with cave dwelling and species jeopardy. However, to hearken briefly back to our ignorance, it is easier (not easy, just easier) to assess the status of cave dwelling bats than the status of bats that are more dispersed in their roosting habits, and thus more difficult to find and monitor. The bias toward cave dwelling bats being on t he threatened list may in part be a result of relative ease of censussing. Life History Traits Predisposing Bats to Extinction Unlike most small mammals, bats have extremely long life spans. Even the smallest bat typically has a life expectancy on the ord er of 10 years, and individuals are known to live much longer than this. Wild little brown bats, for example, are known to survive as long as 30 years (Keen and Hitchcock, 1980). In addition to long life expectancies, bats have very low rates of reproducti on. Many female bats do not reproduce until their second year and, after reaching maturity, females usually produce only a single pup each year. Consequently, bats have far lower potential rates of population growth than are typical of most small mammals. Although bats are often perceived of as similar to rats or mice, the reproductive rates of bats are, in contrast, more similar to those of antelopes or primates. If a bat population is decreased in size, it can recover only slowly. Bats have other charact eristics, which contribute to their vulnerability. Among the most significant is their habit of roosting together in large aggregations. The fact that large numbers of individuals often are concentrated into only a few specific roost sites results in high potential for disturbance. Because of their aggregative roosting habits, species that are very common actually can be vulnerable because they are in only a limited number of roosts. Mexican free tailed bats ( Tadarida brasiliensis mexicana ) are an excellent example. Single cave roosts of these bats can contain 10's of millions of individuals and the loss of even one such roost would mean the loss of a significant portion of the entire species population. Disturbance of Roosts by Humans Aggregations of bats are vulnerable to a variety of human caused disturbances. At least 3 North American nosed bats) are known to have abandoned traditional roost sites because of commercial cave development (Humphrey, 197 8; Tuttle, 1979; Wilson, 1985a). An important hibernaculum for endangered big eared bats has been threatened by quarrying (Hall and Harvey, 1976), and I personally have observed numerous examples of vandalism such as burning old tires, or shooting guns ins ide bat cave roosts. Although intentional disturbance of roosts is well documented, unintentional disturbance often poses an even greater threat. In the temperate zone, Table 1. Officially endangered North American bats* and th eir use of cave roosts. Species Roost Requirements Indiana Bat Myotis sodalis Winter Hibernacula Gray Bat Myotis grisescens Year Round Big Eared Bat§ Plecotus townsendii Year Round Nosed Bat Leptonycteris sanborni Year Round Mexi can Long Nosed Bat Leptonycteris nivalis Year Round *These species are listed on both the IUCN Red List and the U.S. Fish and Wildlife Service Endangered Species List. §Two subspecies of big eared bats are listed: Ozark big eared bat ( P. t. ingens ) and V irginia big eared bat ( P. t. virginianus ).


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 70 aggregations of bats which cavers typically encounter are either hibernating groups tha t occur in late fall, winter, and early spring, or maternity colonies that occur in late spring or summer. There is no question that disturbances as seemingly trivial as merely entering a roost area, or shining a light on hibernating bats or on a maternity group of females and their pups, can result in decreased survival, perhaps outright death, and possible abandonment of the roost site. Although there is some controversy about the my own experience a nd reading of the literature lead me to the opinion that it can be extremely significant. However, there is no question that the impact of such disturbances are somewhat species specific, and that the timing of the disturbance is very important. The resul colony can include the following. (1) It can cause individuals to abandon roost sites, particularly early in the reproductive season when females are pregnant. This may result in females moving to other, perhaps less ideal, roosts where their success at reproducing is reduced. (2) Disturbance raises the general level of activity within roosts. This may result in greater expenditure of energy and less efficient transfer of energy to nursing young. This, in turn, ma y cause slower growth of young and increase the foraging demands on females, thus increasing the time females are outside of the roost and vulnerable to predation. (3) Disturbance can cause outright death of young that lose their roost hold and fall to the cave floor. (4) Maternity aggregations often result in thermoregulatory benefits. Clustering bats gain thermal benefits from being surrounded by other warm bodies. However, individuals also may receive thermal benefit because the accumulated body heat of all individuals present serves to raise temperatures within the roost area. Therefore, if the size of a colony decreases, the accumulated thermal advantages to the individuals in that colony may likewise decrease, and it may become energetically less advan tageous, or perhaps even energetically impossible for females to raise pups in that roost. Thus, there may be a lower size, roost temperatures cannot be raised sufficiently for rearing young and that roost must be abandoned as a maternity site. Problems caused by disturbing hibernating bats also relate to their energy requirements. During winter, temperate zone bats go long periods without eating, and allow their body temperatures to drop, often to ne ar freezing. The energy reserves that bats accumulate prior to hibernation are often close to what is needed to survive the winter. Disturbance during hibernation may cause bats to arouse prematurely, elevating their body temperatures and utilizing stored energy reserves, which should not be spared. The bats may go back into torpor after the disturbance, but then they may not have sufficient energy to survive the rest of winter. This may not be apparent to the person causing the disturbance. Roost site dis turbance also can seriously impact bats, which do not form large aggregations. This is undoubtedly so for many tropical bats, which roost in mature, hollow trees, which are being cut as more tropical forest goes into know the trajectories of populations of any of these tree roosting bats. As an example closer to home, it seems probable that the decline of the Indiana bat may be attributed in part to the loss of roost sites other than caves. Indiana bats hibernate in ca ves and there is no question that disturbance of hibernacula has contributed to their decline. However, in the Midwestern United States, several large hibernacula of Indiana bats are protected from disturbance, yet these cave populations continue to declin e (Clawson, 1987). We can only speculate on the reasons for this continued decline, and this again points to our ignorance. However, while Indiana bats hibernate in caves, in summer they roost and give birth in tree hollows and under the loose bark of tree s. The loss of tree roosts may very well be a serious factor in the continuing decline of the Indiana bat in the Midwest. That the decline of the Indiana bat may be due in part to factors outside of their hibernacula in no way implies that disturbances at hibernacula are unimportant. Rather, it emphasizes the importance of protecting hibernacula so as not to add additional stresses to these populations. Habitat Degradation Outside of Roosts Man also has impacted negatively on bat populations by causing hab itat alteration and degradation outside of their roost sites. For example, two species of North American bats on the red list are endangered, in large part, because species of long nosed bats inhab it desert regions of the Southwestern U.S. and Mexico, and both feed on the nectar and pollen of desert flowers (Wilson, 1985a,b; Anonymous, 1988). Wild agave is a major food source of both species. Wild agaves have been severely reduced because they inter fere with cattle grazing and because they are harvested by moonshiners for making tequila. Although long nosed bat populations also have been


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 71 affected by interference with their cave roosts (Wilson, 1985a, Anonymous, 1988), the reduction in agaves is clear ly important in their decline. Long nosed bats also are major pollinators of both organ pipe and giant Saguaro cacti. The well known decline of these cacti also is evidently directly attributable to the decline of long nosed bats (Wilson, 1985a,b; Anonymou s, 1988). The Role of Pesticides Pesticides used to control insect populations have negatively impacted populations of many bats (Clark, 1981). Two effects seem likely; (1) direct poisoning of bats, and (2) reduction in the resource base of bats which eat insects. At present, we know little regarding the effects caused by pesticides reducing the insect prey of bats. However, direct poisoning by DDT (now banned for use in the U.S.) and other organochlorine pesticides has been widely implicated in the declin e of many bats (reviewed in Clark, 1981). While pesticide poisoning clearly has caused the decline of local populations of many bats, there has been a tendency to over emphasize the importance of pesticide poisoning as one of the major factors in the decli ne of bats (Clark, 1981; McCracken, 1986). In fact, I question whether the general decline of any bat species can be attributed solely or even largely to the toxic effects of pesticides. This is not to exonerate pesticides, but rather to point more strongl y at what are the major causes of bat population declines: i.e., roost site interference and the reduction of resources. I suspect that overemphasis of the importance of pesticide poisoning serves to draw attention away from these other causes. How do I j ustify these statements? First, the belief that bats are unusually sensitive to pesticides dates from an early paper which purported to document their extreme susceptibility to DDT poisoning (Luckens and Davis, 1964). It is now established that the suscept ibility of bats to DDT is in general no greater than that of other similar sized animals (Clark, 1981). Second, there have been many observed, dramatic declines of bat populations that have been attributed to DDT poisoning, without strong data to support t hese attributions. The most spectacular of these occurred in Eagle Creek Cave, Arizona, where the population of Mexican free tailed bats declined from an estimated 30 million to an estimated 30 thousand individuals. While other toxins, such as methyl parat hion (Clark, 1986), may have contributed to this decline, and human disturbance also seems a likely culprit, there is no evidence that DDT poisoning was a major cause of the loss of this population (Clark, 198 1; McCracken, 1986). Again, this is not to say that DDT or other toxins have not directly killed bats. It is well documented, for example, that young Mexican free tailed bats from Carlsbad Caverns have had potentially lethal pesticide concentrations. However, this is evidently a local problem that has not been reported in other colonies of this species DDT poisoning has been done for us. In the early 1960's, Cave Springs Cave in Alabama housed a major maternity colony of gray bats. This cave was heavily disturbed by humans and by the early 1970's all its gray bats were gone. However, Cave Springs Cave was then protected by fencing and its gray bat population began recovering to the point that it now houses an estimated 50,000 individuals. Cave Sp rings Cave is near a former DDT processing plant which also was a major toxic waste dumping site. At present, the bats and bat guano within this cave are substantially polluted with a variety of toxic A lthough, this bat colony experiences occasional dieoffs resulting from these toxins, the colony has nonetheless continued to recover in the face of these pollutants; this recovery dating from when the cave was protected (Tuttle, 1986). Red Caves/Green Cav es From what we know about human caused impacts on bat populations, there is little question that roost site disturbance, vandalism, and habitat destruction have had severe effects. This is particularly so for cave dwelling bats. My opinion that these impa cts are likely to have had greater negative effects than pesticide poisoning is shared by other researchers (Clark, 1981; Tuttle, 1985). People who visit caves, either professionally or for sport, must be acutely aware of the potential damage they can do t o resident bats. To minimize such damage, we should not be visited by humans at any time, or only visited bats or other threatened species and can be open to visitation. Bats select caves as hibernacula or as maternity sites because they fulfill very specific requirements. Fulfilling these requirements depends on cave structure, air circulation patterns, temp relative to foraging sites (Tuttle and Stevenson, 1978; Tuttle, 1979). Because the requirements of bats are highly specific, those caves which do fulfill them will be relatively rare and may be absolutely essential to the bats. There may simply be no acceptable, alternative roost sites


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 72 available. These caves must be placed on our red list. Conversely, most caves will not satisfy these requirements and will not be important as bat roosts. These can be placed on a gre en list. It seems likely that the vast majority of caves would go on the green list. For example, less than 5% of caves surveyed in the southeastern U.S. were found to be physically suitable as gray bat maternity or hibernating roost sites (Tuttle, 1979). A major problem, of course, will be deciding whether a cave belongs on the green versus the red list. One obvious criterion is that major hibernacula and maternity roosts of threatened or declining bats should be red listed, at least during the seasons wh en bats are present. Conversely, caves which are not occupied by bats and for which there is no evidence of prior occupancy should be green listed. But, obviously, judgments will have to be made, often with only limited information. For example, it can be argued that historically important roosting sites that are now abandoned should be red listed, at least temporarily, in the hope that they will be reoccupied. It also can be argued that caves with only small colonies should be red listed, possibly for gene pool conservation, or that caves important to transients during seasonal movements should be red listed during the relevant seasons. On the other hand, there may be no harm in green listing some cave roosts of abundant, widely dispersed species (e.g., tho se of eastern pipistrelles), particularly if those caves have inherent interest to cavers. Although listing caves for no or restricted access because of their use by roosting bats is likely to be controversial, these listings are necessary to preserve bat populations. Individuals who explore caves for sport or scientific study have a high probability of encountering roosting bats. The NSS as the largest single organization of cavers has the opportunity to provide education regarding potential impacts on ba t populations to large numbers of people who are likely to encounter bats. In addition, cavers often have knowledge of bat roosting sites, and this knowledge is essential to informed and responsible listing of caves on red or green lists. Opportunities are abundant for cavers to cooperate with state, national, and private conservation agencies in identifying and preserving sensitive cave habitat. Several NSS grottos have taken the initiative themselves to construct, or are in the process of constructing, re d and green lists of caves. These people should be supported in their efforts. Efforts to construct these lists should be expanded. References Anonymous. 1988. Long nosed bats proposed for endangered status. Bats 6(2): 3. Barbour, R. W., and W. H. Davis . 1969. Bats of America . Univ. of Kentucky Press. Clark, D. R., Jr. 1981. Bats and environmental contaminants: a review . U.S. Fish and Wildlife Service Spec. Sci. Rept. #235. Clark, D. R., Jr. 1986. Toxicity of methylparathion to bats: mortality and coordi nation loss. Envir. Toxicol. Chem ., v. 5: 191 195. Clawson, R. L. 1987. Indiana bats, down for the count. Endangered Species Tech. Bull . XII (9): 9 11. Diamond, J. M. 1988. Red books or green lists? Nature , v. 332: 304 305. Geluso, K. N., J. S. Altenbach, and D. E. Wilson. 1981. Organochlorine residues in young Mexican free tailed bats from several roosts. Amer. Midl. Nat ., v. 105: 249 257. Hall, J. S., and M. J. Harvey. 1976. Petition to place the Virginia big eared bat Plecotus townsendii virginianus, and the Ozark big eared bat Plecotus townsendii ingens, on the U.S. Fish and Wildlife Service "List of Endangered Species." Humphrey, S. R. 1978. Status, winter habitat, and management of the endangered Indiana bat, Myotis sodalis. Florida Sci ., v. 41: 65 76. Imboden, C. 1987. Green lists instead of red books? World Birdwatch , v. 9(2): 2. Keen, R., and H. B. Hitchcock. 1980. Survival and longevity of the little brown bat (Myotis lucifugus) in southeastern Ontario. J. Mammal ., v. 61: 1 7. Luckens, M. M., and W. H. Davis. 1964. Bats: sensitivity to DDT. Science , v. 146: 948. McCracken, G. F. 1986. Why are we losing our Mexican free tailed bats? Bats , v. 3: 1 4. Tuttle, M. D. 1979. Status, causes of decline and management of endangered gray bats. J. Wildl. Manag ., v. 43: 1 17. 7. Tuttle, M. D. 1986. Endangered gray bat benefits from protection. Bats , v. 4(4): 1 4. Tuttle, M. D., and D. E. Stevenson. 1978. Variation in the cave environment and its biological implication. Proc. Nat'l Cave Management Symp . (R. Zuber, J. Chester, S. Gilbert, and D. Rhoades, eds.), pp. 108 121. Wilson, D. E. 1985a. Status Report: Leptonycteris sanboni, Horfmeister. Sanborn's long nosed bat. Rept. to U.S. Fish and Wildlife Service, 35 pp. Wilson, D. E. 1985b. Status Report: Leptonycteris nivalis, Saussure. Mexican long nosed bat. Rept. to U.S. Fish and Wildlife Service, 33 pp.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 73 Thermal Requirements During Hibernation Merlin D. Tuttle and Jim Kennedy Bat Conservation International, P.O. Box 162603, Austin, TX 78716 Abstract We monitored te mperatures for up to 2 years at 15 of the most important sites for hibernation of Indiana bats ( Myotis sodalis ). Comparison of temperatures at successful and unsuccessful sites revealed that populations occupying roosts with midwinter (December February) t emperatures of 3.0 7.2°C increased by 97,339 bats over the past 20 years, whereas populations hibernating at temperatures outside this range decreased by 185,117 animals. In all but the northernmost range of Indiana bats, caves and mines required for succe ssful hibernation must provide chimney effect internal environment to minimize risk of freezing. Protection of caves and mines providing these exceptional characteristics and restoration of appropriate temperatures in altered sites is essential for recovery of the Indiana bat. Key words : caves, hibernation, Indiana bat, management, mines, Myotis sodalis , population, temperature Introduc tion In the early 1800s, the Indiana bat ( Myotis sodalis ) mammals, with possibly millions occurring in single caves (Silliman et al. 1851, Tuttle 1997). Nonetheless, by 1980, fewer than 700,000 bats remained, and size of the population fell to 382,000 bats by 2001 (Clawson 2002). The greatest losses occurred in discrete, unrelated episodes that rendered overwintering caves no longer suitable for hibernation, mostly due to reductions in size e, which ultimately raised internal temperatures (Humphrey 1978). Increases of as little as (Tuttle 1977). Humphrey (1978), however, concluded that such losses were reversible, because restoration of acceptable temperatures led to prompt recovery at some sites. Nevertheless, specific temperatures required by Indiana bats during hibernation are not understood completely. Our purpose is to compare annual patterns of temperature in hibernacula where popu lations of Indiana bats have been successful with temperatures in hibernacula where populations are declining. In addition, we indicate correctable deficiencies at important sites of current and past use and suggest characteristics for evaluating roosts fo r protection or restoration. Methods We evaluated patterns of temperature at 15 of the most important, current and past, hibernating sites of Indiana bats, in caves and mines of Illinois, Indiana, Kentucky, Missouri, Tennessee, and Virginia (Fig. 1). To monitor temperature, we used 60 dataloggers (Model Hobo Pro Temp RH, Onset Computer Corporation, Pocasset, Massachusetts) in 1998 and 58 instruments in 1999. A datalogger was installed within each hibernaculum, at each site that was favored by hibernating Indiana bats, either currently or in the past. Another datalogger was positioned outside each cave or mine to monitor external conditions, except at the Magazine Mine. All instruments recorded data at 3 h intervals. Although dataloggers recorded temperatur e and relative humidity, we found no evidence of an effect of humidity beyond that indicated by temperature, so humidity was not included in our analyses. Most dataloggers were installed in July 1998 and downloaded in July, August, or September 1999 and a gain in 2000. When dataloggers were installed in 1998 Figure 1 . Range of the Indiana bat and location of hibernacula in which we monitored temperature.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 74 (except at the Magazine Mine), temperatures of the air and wall of the cave also were measured at each roosting site, using a portable digital thermometer (Model 2300 PNC5, IMC Instruments, Inc., Menomo nee Falls, Wisconsin) that was recalibrated prior to each field trip. Temperatures indicated by the dataloggers at time of installation differed, on average, by less than 0.3 °C (range = 0.0 0.4°C; n = 31 sites) from wall At time of downloading in 1999, a sample of 10 dataloggers from five caves provided readings that again averaged within 0.3°C (0.0 0.7°C) of those obtained with the digital thermometer. In addition, controlled tests of random batches of dataloggers yielded similar average variation (0.3°C) . We also evaluated ability of each hibernaculum to buffer the internal environment against changes in the external environment, using an index of temperature variability: V = (T max roost T min roost )/(T max surface T min surface ) , where T represents m aximum or minimum temperature recorded at the roost or outside the hibernaculum, as indicated by the subscripts. A small value of V indicates a stable internal environment that varies little with changing external conditions; a large value of V indicates a less stable, more variable, internal environment. Results In both 1998 1999 and 1999 2000, 43 dataloggers recorded temperatures year round. Although 17 loggers failed the 1 st year and 15 malfunctioned during the 2 nd year, only two of 32 malfunctions were caused by operator error. The others were due to problems such as moisture bypassing past dirty seals, moisture entering through cracked housings, or an increased internal Figure 2. External ambient temperatures and tempearature at the main hibernation site in Great Scott Cave, Misso uri before and after opening a blocked entrance in September 1999.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 75 resistance that developed within the lithium batteries initially supplied by the ma nufacturer. Nevertheless, most failures occurred after the hibernation season, thus minimizing loss of data. Overall, temperatures at the 15 hibernacula in midwinter (December February) were similar between years (Tables 1 4). Average mean temperature with in hibernacula was 6.8°C in 1998 1999 and 6.5°C in 1999 2000, while average mean surface temperatures were 3.5°C and 3.0°C for the same periods. Midwinter means at individual hibernacula varied by less than 1°C between years at all locations, except Great Scott Cave. In addition, changes between years in mean midwinter temperature inside hibernacula always were in the same direction as changes on the surface, again with the exception of Great Scott Cave. Temperature in Great Scott Cave decreased by 3.6°C b etween years, despite an increase of 0.4°C in surface temperature, following reopening of a previously blocked entrance (Fig. 2). Given the similarity in temperatures between years, we typically restrict further discussion to data obtained in the 1 st year for simplicity. Individual caves differed by almost a factor of eight in ability to buffer changes in external temperature, as indicated by the index of variability. In December February 1998 1999, the index of variability for Rocky Hollow and Wyandotte caves was 0.05; White Oak Blowhole, 0.06; Saltpeter Cave, 0.08; Saltpetre Cave, 0.09; Bat Cave, Kentucky, 0.10; Pilot Knob Mine, 0.11; Linefork Cave, 0.12; Great Scott Cave, 0.13; Twin and Bat Cave, Mis souri, 0.38. Dataloggers failed during the first winter at Batwing Cave, but the comparable index in 2000 was 0.02. External temperatures were not monitored at the Magazine Mine, so we could not calculate an index for it. Annual temperature profiles for so me caves of low to medium variability (medium to high stability) are shown in Figure 3. We also examined roost temperatures and changes in population size at seven caves and mines that we monitored, using data on temperature and population provided by t he Indiana Bat Recovery Team (Table 5). Hibernacula where populations grew provided roost temperatures of 3.0 7.2°C, whereas populations fell at hibernacula with temperatures outside that range. At Great Scott Cave, the population increased by 22,800 bats between 1976 and 1979, when internal temperatures averaged 4.8°C, but declined by 46,625 bats between 1980 and 1997, when temperatures averaged 8.1°C, following closure of an entrance. Discussion The ideal situation Caves that historically sheltered the l argest populations of hibernating Indiana bats, without exception, were those that provided the largest volumes and structural diversity, ensuring the most stable internal temperatures, over the widest ranges of external temperature, with the least likelih ood of freezing. Such caves also provide chimney effect airflow, typically through multiple entrances, and trap and store cool winter air in low areas (Tuttle and Stevenson 1978). Within such caves, hibernating Indiana bats prefer temperatures of 3 6°C in midwinter (Hall 1962, Henshaw and Folk 1966). Although metabolism of hibernating bats is lowest at temperatures slightly above 0°C, Indiana bats are forced to increase production of metabolic heat or arouse from torpor as temperatures fall to 0°C and below . They also arouse in response to abrupt changes in ambient temperature (Davis and Reite 1967, Henshaw and Folk 1966). Thus, roosts with the most stable temperatures should result in fewest arousals, thereby minimizing energy expenditure (Thomas et al. 199 0). Recent and historic populations of hibernating Indiana bats support these conclusions. For example, Mammoth system, with a length of 571 km. Staining left on walls and ceilings of Mammoth Cave (Toomey et al. 2002) suggests that this cave once sheltered the largest hibernating population of Indiana bats, conservatively estimated at ca. 10 million animals (Tuttle 1997). In addition, comparison of other populations of Indiana bats that remained stable or i ncreased with those that declined over the past 20 years (Table 5) strongly implies that inappropriate temperatures at hibernating Figure 3. Annual profiles of temperature for unusually successful hibernacula of the Indiana bat.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 76 sites are a primary cause of decline, as suggested by Humphrey (1978). We believe that temperature profiles documented for R ocky Hollow Cave, Magazine Mine, and Pilot Knob Mine (Fig. 3) most closely approximate ideal hibernating conditions for the Indiana bat. Through the entire annual cycle (not just midwinter) of 1998 1999, Rocky Hollow Cave remained at 5.6 7.6°C; Magazine Mi ne, at 1.4 6.9°C; and Pilot Knob Mine, at 3.1 7.7°C. hibernating temperatures is achieved through the buffering effects of very large volume. Not surprisingly, these three sites have histories o f extraordinary success at supporting hibernating populations of Indiana bats. Rocky Hollow Cave prior to the onset of intense human disturbance, and the population of Indiana bats at the Magazine Mine g rew to nearly 15,000 bats in only a few years after the mine closed (Kath 2002). Pilot Knob Mine also rapidly attracted a hibernating population of at least 100,000 Indiana bats soon after it became available, though subsequent collapse has prevented furth er censuses (Clawson 2002). Effects of restoring airflow Comparison of annual cycles before and after reopening a blocked entrance illustrates that management efforts can restore unacceptably altered roost temperatures. The population at Great Scott Cave (Fig. 2, Tables 1, 3, and 5) was growing prior to blockage of its second entrance in summer 1978, after which roost temperature rose by at least 3.3°C and the population decreased by 80%. After the entrance was reopened in September 1999, average internal temperatures decreased by 3.6°C, even though outside temperatures averaged 0.4°C higher in winter 1999 2000 than in the previous winter. Consequently, temperatures at the roost were within the ideal, 3 6°C range on 61 days during 1999 2000, greatly improvi ng from only 1 day in the entire previous hibernating season. We anticipate that the population at Great Scott Cave, with return of more appropriate hibernating temperatures, will again begin to grow, as happened at Wyandotte Cave. The entrance to this c ave was mostly blocked by a masonry wall that was removed in 1977 (see fig. 4 in Currie 2002). Afterwards, temperatures in Wyandotte Cave decreased, and the population grew by 90% (Johnson et al. 2002, Richter et al. 1993). Nevertheless, temperatures in Wy andotte Cave (Tables 1 and 3) remain too high, in our opinion, to permit reestablishment of a historic sized population of Indiana bats. Staining on the walls and ceiling in Wyandotte Cave suggest a much larger past population that possibly numbered in th e millions. The current population, despite encouraging recovery, is no more than a small fraction of its presumed former size. Results of temperature monitoring strongly suggest that this population could be expanded substantially with further lowering of internal temperature. Stability of internal temperature in Wyandotte Cave already is similar to that of Rocky Hollow Cave ( V = 0.05 for both; Tables 1 and 3), probably contributing greatly to the level of recovery already achieved at Wyandotte Cave. An ad ditional decrease of 5°C would further enable large numbers of bats to hibernate in traditional roosts beyond areas now disturbed by commercial tours in winter (Johnson et al. 2002), probably permitting even greater recovery. Are we protecting marginal si tes? Knowledge of energetics during hibernation, historical conditions chosen by the largest hibernating populations, and temperature profiles that we provide, strongly suggest that a large proportion of currently protected sites are marginal, at best, in terms of long term survival of the Indiana bat. To understand better what is required to rebuild historically large populations, one must consider energy budget. When inappropriate temperatures or rapid fl uctuations in temperature cause arousal and increase the cost of hibernation, less energy remains for surviving unusually stressful winters or unpredictable weather during spring migration. Summer nursery roosts that provide marginally warm temperatures or that are distant from good feeding habitat result in extra energy expenditure and slower growth of young in insectivorous bats (Tuttle 1975, 1976a). Late fledging leads to low body mass in autumn (Humphrey et al. 1977), and this can make the cost of lon g distance migration, already an important mortality factor, prohibitive (Tuttle 1975, 1976b; Tuttle and Stevenson 1977). Hibernation sites sheltering the largest populations of Indiana bats require the longest average migrations from suitable summer habit ats, because these hibernacula serve animals from the largest geographic areas. Also, long autumn migrations may require as much energy as an entire winter of hibernation (Tuttle 1976b), so it seems that the very substantial costs of


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 77 marginal hibernating conditions cannot be borne by bats having to make long migrations. When hibernating conditions deteriorate and large populations decline due to significant disturbance and/or altered roost temperatures, a small proportion of the population usually survive s in the now marginal hibernaculum. Size of this proportion undoubtedly is determined by the amount of added costs that are imposed by the disturbance or altered microclimate during hibernation. In contrast, the relatively few bats that summer in more idea l conditions near the hibernaculum avoid the costs of autumn and spring migration, thereby conserving substantial energy that can be spent on hibernation, as well as on surviving unpredictable spring weather. Those that use l ess than optimal summer habitat or migrate long distances may not have sufficient energy available to meet the new demands and may succumb over winter. Also, some small populations that continue using marginal caves appear stable only because of annual immigration of bats from more suc cessful populations at more ideal hibernacula. For example, ca. 1,000 2,000 Indiana bats hibernated in Wyandotte Cave each winter before 1978, i.e., before removal of the wall that elevated winter temperatures. Richter et al. (1993), based on body mass dyn amics, estimated that survivorship of hibernating individuals at this time was not high enough to sustain the population and that apparent stability of the population at Wyandotte Cave actually was due to an influx of bats each year from other hibernacula. Their data suggested annual mortality rates of 45% during hibernation in Wyandotte Cave, compared with 1% in a cooler hibernaculum, Twin Domes Cave, which was located nearby. Buffering climatic extremes Although suitable roost temperature profiles are im buffer climatic extremes is also critical. For example, our temperature profiles from Bat Cave, in Missouri, illustrate that it is a mortality trap. Although Bat Cave provides ideal temperatures in autumn, it often falls well below freezing in winter, and Indiana bats attracted to this cave in autumn risk freezing to death before spring (Tables 1 and 3). Our data suggest that some caves with currently stable or growing populations also are mortality traps that more seriously threaten survival of the species than do sites like Bat Cave, Missouri. Small, simple sites, such ideal internal temperatures over long enough periods that a large population develops between lethal, external extremes in temperature. Range of internal temperatures at th ese two caves, during December February 1998 1999, was 7.8 and 6.7°C, respectively, compared with nearby Wyandotte Cave, with a range of 2.3°C (Table 1). By comparing indices of temperature vari ability at V = 0.16) and Twin Domes (0.15) caves are 3.2 and 3.0 times less stable than Wyandotte Cave (0.05), which probably was the traditional, primary hibernaculum for the region. Differences in stability were even more pronounced Twin Domes caves were 4.3 and 5.0 times less stable, respectively. Average surface temperature for January consequently, internal temperatu res were 0.7°C higher. In contrast, a 1.3°C external rise at Wyandotte Cave raised roost temperatures only 0.2°C. Mean temperatures for January over the past 100 years in that area of Indiana ranged from 4.9°C, in 1950, to 10.2°C, in 1977, a difference of 15.1°C (http://, South Central Indiana Division). This large difference among years extremely vulnerable over several decades, and emphasizes the importance of r estoration efforts at former key bastions of survival, such as Wyandotte, Rocky Hollow, and Mammoth caves (e.g., Toomey et al. 2002), that are more stable. Comments on other hibernacula Efforts to restore temperature are also in progress at Coach Cave, th e former home of at least 100,000 Indiana bats. Internal temperatures appear suitable, but fluctuations in December February 1999 2000 (Table 3) are still 3.2 and 3.5 times greater than those at Wyandotte and Rocky Hollow caves, respectively. Such instabil ity, along with rapid airflow through roosting areas, may explain current failures to restore the population at this site (Currie 2002). Cooler temperatures and airflow may be due to an artificial entrance that remains open, although past enlargement of pa ssages for use by tourists also may be a factor. This is definitely a correctable problem that should receive high priority. Linefork Cave is another site of a large past population, and it appears to have an adequate temperature profile to justify a popul ation larger than it currently has. We suspect that disturbance remains an issue here. The cave is popular with cavers, and an entrance (Dungeon


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 78 Entrance) that leads through the primary area of past use by bats, remains unprotected. Our data suggest that Bat Cave, Kentucky, is a site of secondary importance, compared with nearby Saltpetre Cave, which is another apparently essential hibernaculum of the past. Staining indicates a historic population of perhaps a million Indiana bats at Saltpetre Cave prior t o extensive mining of nitrate during the War of 1812, followed by use of the cave for commercial tours. Remnants of its population of Indiana bats apparently reside in Bat Cave. Physical alterations resulting from mining and commercialization probably caus e temperatures to be slightly higher than the optimum for Indiana bats (Tables 1 and 3), but Indiana bats still should prefer Saltpetre Cave to Bat Cave temperatures ( V = 0.08 for Saltpetre Cave and V = 0.10 for Bat Cave; Tables 1 and 3). A cessation of commercial tours during hibernation, beginning in winter 1998 1999, likely is responsible for an increase in population, from 475 bats in 1999 to 1,225 bats in 2001. Research on how best to restore ideal temperatures is underway, and we believe this site offers excellent potential for further recovery. Conclusions Available evidence strongly suggests that protection of hibernacula from disturbance by humans is critically important, yet it is insufficient if not accompanied by restoration of appropriate temperatures. All populations of which we are aware, which are not jeopardized by inappropriate temperatures, disturbance, or flooding, are stable or growing, indicating that problems during hibernation like decline. Degradation of summer feeding and roosting habitats is probably a contributing factor in decline of Indiana bats. Nevertheless, restoration of required temperatures and protection of essential hibernatin g sites is vital to recovery, and we agree with Humphrey (1978) that losses are reversible through restoration. We suggest that resource managers make immediate efforts to identify and correct deficiencies in temperature at major caves of past or current use. In addition, we suggest that abandoned mines now provide some of the best options for large scale restoration of the population, due to the enormous size of some mines, the resulting stability of temperature, and the multiple entrances to many mines t hat cause chimney effect airflow (e.g., Kath 2002). Furthermore, we emphasize that significant hibernacula of the past may not be occupied currently and that other sites of historic use remain undiscovered. Such sites easily are identified by a combination of temperature, roost staining, and a structure that traps cold air; these caves may need nothing more than protection from disturbance or removal of material blocking the entrance to restore large populations of Indiana bats. Finally, all cave entrances essential to proper cooling of key hibernating sites must be identified and protected from inadvertent closures, including those that may occur naturally. Most caves that once served as bastions of survival for Indiana bats already have been lost to commer cialization or closure, and those that remain require careful management if this species is to recover. Acknowledgments Carter Caves State Resort Park on their recent leadership in protecting Rocky Ho llow and Saltpetre Wyandotte Caves State Recreation Area for substantial progress at restoration of Wyandotte Cave. Primary funding for this project was provided by the U.S. Fish and Wildlife Service, U.S. F orest Service, U.S. Environmental Protection Agency, National Fish and Wildlife Foundation, Bass Foundation, and David and Lucile Packard Foundation. We are deeply indebted to the following individuals for assistance in the past 3 years: S. Amelon, S. Beam , V. Brack, E. Br itzke, R. Clawson, R. Currie, Ja . DePew, Je. DePew, K. Dunlap, W. Elliott, R. Gleitz, M. Gumbert, C. Hobson, F. Johnson, S. Johnson, J. Kath, D. Kemper, J. MacGregor, N. Michie, P. Moosman, L. Nutt, B. Palmer Ball, S. Plummer, S. Reis, R. Reynolds, B. Schwartz, M. Spanel, J. Thomison, N. Thomison, J. Tierney, T. Wethington, and S. Widowski. Additional dataloggers and field support were provided by George Washington Jefferson National Forests, Great Smoky Mountains National Park, Illinois De partment of Natural Resources, Indiana Department of Natural Resources, Kentucky Nature Preserves, Kentucky State Parks, Missouri Department of Conservation, Park Mammoth Resort, Shawnee National Forest, and Wyandotte Caves State Recreation Area. We also t hank numerous private landowners and agencies for allowing access to their caves and mines and for supporting recovery efforts for the Indiana bat. Literature Cited Clawson, R. L. 2002. Trends in population size and current status. In The Indiana bat: bio logy and management of an endangered species (A. Kurta and J. Kennedy, eds.). Bat Conservation International, Austin, Texas.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 79 Currie, R. R. 2002. Response to gates at hibernacula. In The Indiana bat: biology and management of an endangered species (A. Kurta and J. Kennedy, eds.). Bat Conservation International, Austin, Texas. Davis, W. H., and O. B. Reite. 1967. Responses of bats from temperate regions to changes in ambient temperature. Biological Bulletin 132:320 328. Hall, J. S. 1962. A life history and ta xonomic study of the Indiana bat, Myotis sodalis . Reading Public Museum and Art Gallery, Scientific Publications 12:1 68. Henshaw, R. E., and G. E. Folk, Jr. 1966. Relation of thermoregulation to seasonally changing microclimate of two species of bats ( Myo tis lucifugus and M. sodalis ). Physiological Zoology 39:223 236. Humphrey, S. R. 1978. Status, winter habitat, and management of the endangered Indiana bat, Myotis sodalis . Florida Scientist 41:65 76. Humphrey, S. R., A. R. Richter, and J. B. Cope. 1977. S ummer habitat and ecology of the endangered Indiana bat, Myotis sodalis . Journal of Mammalogy 58:334 346. Johnson, S. A., V. Brack, Jr., and R. K. Dunlap. 2002. Management of hibernacula in the state of Indiana. In The Indiana bat: biology and management o f an endangered species (A. Kurta and J. Kennedy, eds.). Bat Conservation International, Austin, Texas. Kath, J. A. 2002. An overview of hibernacula in Illinois, with emphasis on the Magazine Mine. In The Indiana bat: biology and management of an endangere d species (A. Kurta and J. Kennedy, eds.). Bat Conservation International, Austin, Texas. Richter, A. R., S. R. Humphrey, J. B. Cope, and V. Brack, Jr. 1993. Modified cave entrances: thermal effect on body mass and resulting decline of endangered Indiana b ats ( Myotis sodalis ). Conservation Biology 7:407 415. Silliman, B., Jr. 1851. On the Mammoth Cave of Kentucky. American Journal of Science and Arts (Second Series) 11:332 339. Thomas, D. W., M. Dorais, and J. M. Bergeron. 1990. Winter energy budgets and co st of arousals for hibernating little brown bats, Myotis lucifugus . Journal of Mammalogy 71:475 479. Toomey, R. S., III, M. L. Colburn, and R. A. Olson. 2002. Paleontological evaluation of past use of caves by: a significant tool for restoration of hiberna cula. In The Indiana bat: biology and management of an endangered species (A. Kurta and J. Kennedy, eds.). Bat Conservation International, Austin, Texas. Tuttle, M. D. 1975. Population ecology of the gray bat ( Myotis grisescens ): factors influencing early growth and development. University of Kansas, Occasional Papers of the Museum of Natural History 36:1 24. Tuttle, M. D. 1976a. Population ecology of the gray bat ( Myotis grisescens ): factors influencing growth and survival of newly volant young. Ecology 57 :587 595. Tuttle, M. D. 1976b. Population ecology of the gray bat ( Myotis grisescens ): philopatry, timing and patterns of movement, weight loss during migration, and seasonal adaptive strategies. University of Kansas, Occasional Papers of the Museum of Nat ural History 54:1 38. Tuttle, M. D. 1977. Gating as a means of protecting cave dwelling bats. Pp. 77 82 in 1976 National Cave Management Symposium proceedings (T. Aley and D. Rhodes, eds.). Speleobooks, Albuquerque, New Mexico. Tuttle, M. D. 1997. A Mammot h discovery. Bats 15:3 5. Tuttle, M. D., and D. Stevenson. 1977. An analysis of migration as a mortality factor in the gray bat based on public recoveries of banded bats. American Midland Naturalist 97:235 240. Tuttle, M. D., and D. Stevenson. 1978. Varia tion in the cave environment and its biological implications. Pp. 108 121 in 1977 National Cave Management Symposium proceedings (R. Zuber, J. Chester, S. Gilbert, and D. Rhodes, eds.). Adobe Press, Albuquerque, New Mexico. U.S. Fish and Wildlife Service. 1999. Agency draft. Indiana bat ( Myotis sodalis ) revised recovery plan. Fort Snelling, Minnesot a.


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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 83 Ecological Impacts of W ind E nergy D evelopment on B ats: Q uestions, R esearch N eeds, and H ypotheses Thomas H Kunz 1 * , Edward B Arnett 2 , Wallace P Erick son 3 , Alexander R Hoar 4 , Gregory D Johnson 3 , Ronald P Larkin 5 , M Dale Strickland 3 , Robert W Thresher 6 , and Merlin D Tuttle 2 1 Center for Ecology and Conservation Biology, Boston University, Boston, MA * (; 2 Bat Conservation International, Austi n, TX; 3 Western EcoSystems Technology Inc, Cheyenne, WY; 4 US Fish and Wildlife Service, Hadley, MA; 5 Illinois Natural History Survey, Champaign, IL; 6 National Renewable Energy Laboratory, Golden, CO Front Ecol Environ 2007; 5(6): 315 324 Abstract At a ti me of growing concern over the rising costs and long term environmental impacts of the use of fossil fuels and nuclear energy, wind energy has become an increasingly important sector of the electrical power industry, largely because it has been promoted as being emission free and is supported by government subsidies and tax credits. However, large numbers of bats are killed at utility scale wind energy facilities, especially along forested ridge tops in the eastern United States. These fatalities raise impo rtant concerns about cumulative impacts of proposed wind energy development on bat populations. This paper summarizes evidence of bat fatalities at wind energy facilities in the US, makes projections of cumulative fatalities of bats in the Mid Atlantic Hig hlands, identifies research needs, and proposes hypotheses to better inform researchers, developers, decision makers, and other stakeholders, and to help minimize adverse effects of wind energy development. W ind energy has become an increasingly importa nt sector of the renewable energy industry, and may help to satisfy a growing worldwide demand for electricity (Pasqualetti et al . 2004; GAO 2005; Manville 2005). Environmental benefits of wind energy accrue from the replacement of energy generated by othe r means (e . g ., fossil fuels, nuclear fuels), reducing some adverse environmental effects from those industries (Keith et al . 2003). However, development of the wind energy industry has led to some unexpected environmental costs (Morrison and Sinclair 2004) . For example, soaring and feeding raptors have been killed in relatively large numbers in areas of high raptor abundance in the United States and Europe (Barrios and Rodriquez 2004; Hoover and Morrison 2005). More recently, large numbers of bat fatalities have been observed at utility scale wind energy facilities, especially along forested ridge tops in the eastern US (Arnett 2005; GOA 2005; Johnson 2005; Fiedler et al . 2007), and in agricultural regions of southwestern Alberta, Canada (RMR Barclay and E B aerwald pers comm). Similar fatalities have been reported at wind energy facilities in Europe (UNEP/Eurobats 2005; Brinkmann et al . 2006). As such facilities continue to develop in other parts of the world, especially in Australia, China, and India (Nation al Wind Watch Inc 2006), increased numbers of bat and bird fatalities can be expected. In this paper, we highlight ongoing development of wind energy facilities in the US, summarize evidence of bat fatalities at these sites, make projections of cumulative fatalities of bats for the Mid Atlantic Highlands (MD, PA, VA, and WV), identify research needs to help reduce or mitigate adverse environmental impacts at these facilities, and propose hypotheses to evaluate where, when, how, and why bats are being kille d. Utility scale wind energy development in the US In 2005, utility scale wind energy facilities in the US accounted for approximately 9616 MW of installed capacity (also called name plate capacity or the potential generating capacity of turbines; EIA 20 06). The number and size of wind energy facilities have continued to increase, with taller and larger turbines being constructed. Available estimates of installed capacity in the US by 2020 range up to 72, 000 MW, or the equivalent of 48, 000 1.5 MW wind tur bines. This is enough, according to some projections, to account for generating capacity. Most existing wind energy facilities in the US include turbines with installed capacity ranging from 600 kW to 2 MW per turbine. Wind t urbines up to about 3 MW of installed capacity for onshore applications are currently being tested. However, owing to seasonally variable wind speeds, the generating capacity of most existing wind turbines is less than 30% of installed capacity.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 84 Utility sc ale wind turbines (> 1 MW) installed in, or planned for, the US since the 1990s are designed with a single monopole (tubular tower), ranging in height from 45 to 100 m, with rotor blades up to 50 m in length. At their greatest height, blade tips of typical 1.5 MW turbines may extend to 137 m (as tall as a 40 story building with a rotor diameter the size of a 747 jumbo jet). The nacelle, located at the top of the monopole, houses a gearbox that is connected to an electric generator and associated electronic converters and controls. Three rotor blades are attached to a drive shaft that extends outward from the nacelle. The pitch or angular orientation of the three blades can be adjusted to control turbine output and rotation speed of the rotor. Typically, wind turbines are arranged in one or more arrays, linked by underground cables that provide energy to a local power grid (WebFigure 1). Some modern turbines (e . g ., GAMESA G87 2.0 MW turbine) rotate up to 19 rpm, driving blade tips at 86 m s 1 (193 mph) or more . Since utility scale wind turbines were first deployed in the US in the 1980s, the height and rotor swept area has steadily increased with each new generation of turbines. To date, most utility scale wind turbines in the US have been installed in grassla nd, agricultural, and desert landscapes in western and mid western regions. More recently, however, wind turbines have been installed along forested ridge tops in eastern states (Figure 1). More are proposed in this and other regions, including the Gulf Co ast and along coastal areas of the Great Lakes. Large wind energy facilities off the coastline of the northeastern US have also been proposed. In a nutshell: commonly killed at utility scale wind en ergy facilities in the US and sites with the highest potential for adverse environmental impacts on bats year monitoring and hypothesis based research are needed to address these concerns A policy framework that requires owners and developers to provide full access to publicly supported wind energy facilities should be implemented, and should include funds for research and monitoring at these sites Bat fatalities Relatively small numbers o f bat fatalities were reported at wind energy facilities in the US before 2001 (Johnson 2005), largely because most monitoring studies were designed to assess bird fatalities (Anderson et al . 1999). Thus, it is quite likely that bat fatalities were underes timated in previous research. Recent monitoring studies indicate that some utility scale wind energy facilities have killed large numbers of bats (Kerns and Kerlinger 2004; Arnett 2005; Johnson 2005). Of the 45 species of bats found in North America, 11 ha ve been identified in ground searches at wind energy facilities (Table 1). Of these, nearly 75% were foliage roosting, eastern red bats ( Lasiurus borealis ), hoary bats ( Lasiurus cinereus ), and tree cavity dwelling silver haired bats ( Lasionycteris noctiva gans ), each of which migrate long distances (Figure 2). Other bat species killed by wind turbines in the US include the western red bat ( Lasiurus blossivilli ), Seminole bat ( Lasiurus seminolus ), eastern pipistrelle ( Perimyotis [=Pipistrellus] subflavus ), l ittle brown myotis ( Myotis lucifugus ), northern long eared myotis ( Myotis septentrionalis ), long eared myotis ( Myotis evotis ), big brown bat ( Eptesicus fuscus ), and Brazilian free tailed bat ( Tadarida brasiliensis ). A consistent theme in most of the monito ring studies conducted to date has been the predominance of migratory, tree roosting species among the fatalities. For several reasons (eg cryptic coloration, small body size, steep topography, overgrown vegetation), bats may have been overlooked during p revious carcass searches. Based on recent evaluations of searcher efficiency, on average, only about half of test subjects (fresh and frozen bats or birds) are recovered by human observers (Arnett et al . in press; WebTable 1). In these studies, bats were n early twice as likely to be found in grassland areas as in agricultural landscapes and along forested ridge tops. Moreover, scavengers often remove carcasses before researchers are able to recover them (Arnett et al . in press). To date, no fatalities of s tate or federally listed bat species have been reported; however, the large number of fatalities of other North American species has raised concerns among scientists and the general public about the environmental friendliness of utility scale wind energy f acilities. For example, the number of bats killed in the eastern US at wind energy facilities installed along forested ridge tops has ranged from 15.3 to 41.1 bats per MW of installed capacity per year (WebTable 1). Bat fatalities reported from other regio ns of the western and mid western US have been lower, ranging from 0.8 to 8.6 bats MW 1 yr 1 , although many of these studies were designed only to assess bird fatalities (Anderson et al . 1999). Nonetheless, in a recent study designed to assess bat fatalitie s in southwestern Alberta,


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 85 Canada, observed fatalities were comparable to those found at wind energy facilities located in forested regions of the eastern US (RMR Barclay and E Baerwald pers comm). While the seasonal duration of reported studies, corrections for searcher efficiency and scavenging rates vary geographically, fatality rates have been among the highest reported in the eastern US (Table 1). As research protocols for bats shift toward improved monitoring studies, more bat specie s are likely to be affected and greater measured fatality rates at wind energy facilities are expected. Locations of bat fatalities Bat fatalities at wind energy facilities appear to be highest along forested ridge tops in the eastern US and lowest in rel atively open landscapes in the mid western and western states (Johnson 2005; Arnett et al . in press), although relatively large numbers of fatalities have been reported in agricultural regions from northern Iowa (Jain 2005) and southwestern Alberta, Canada (RMR Barclay and E Baerwald pers comm). Additionally, in a recent study conducted in mixed grass prairie in Woodward County, north central Oklahoma, Piorkowski (2006) found 111 dead bats beneath wind turbines, 86% of which were pregnant or lactating Brazi lian free tailed bats. Western red bats, hoary bats, silver haired bats, and Brazilian free tailed bats have also been reported at wind energy facilities in northern California (Kerlinger et al . 2006). To date, no assessments of bat fatalities have been re ported at wind energy facilities in the southwestern US, a region where large numbers of migratory Brazilian free tailed bats are resident during the warm months (McCracken 2003), and where this species provides important ecosystems services to agriculture (Cleveland et al . 2006). High fatality rates can also be expected for other species in the southwestern US and at wind energy facilities in western states, where rigorous monitoring for bat fatalities has been limited. Seasonal timing of bat fatalities M ost bat fatalities in North America have been reported in late summer and early autumn (Johnson 2005; Arnett et al . in press; RMR Barclay and E Baerwald pers comm), and similar seasonal trends have been reported for bats in northern Europe (Bach and Rahmel 2004; Dü rr and Bach 2004). Migration of tree bats in North America is known to occur from March through May and again from August through November (Cryan 2003). The few bat fatalities reported during spring migration and early summer may reflect the fact that less intensive fatality searches were conducted during this period, but it may also be due to bats migrating at higher altitudes during spring. Many, if not most, of the bat species that have been killed by wind turbines in the US (Table 1 and WebTabl e 1) are resident during summer months (Barbour and Davis 1969). A study by Piorkowski (2006) provided evidence that bats are at risk of being killed by wind turbines during summer, and, thus, more rigorous fatality assessment is warranted during this seas on. In addition to being at risk during migration, the large colonies of Brazilian free tailed bats that disperse nightly across vast landscapes in the southwestern US (McCracken 2003; Kunz 2004) may be at risk during the period of summer residency. Uncert ainty with respect to the seasonality of bat fatalities in North America may, in part, reflect the lack of full season, multi year monitoring studies that include spring and autumn migratory periods as well as summer months, when bats are in residence (Arn ett et al . in press). How and why are bats being killed? It is clear that bats are being struck and killed by the turning rotor blades of wind turbines (Horn et al . in press). It is unclear, however, why wind turbines are killing bats, although existing s tudies offer some clues. Are bats in species are known to seek the nearest available trees as daylight approaches (Cryan and Brown in press), and thus could mistake large monopoles for roost trees (Ahlén 2003; Hensen 2004). Tree roosting bats, in particula r, often seek refuge in tall trees (Pierson 1998; Kunz and Lumsden 2003; Barclay and Kurta 2007). As wind turbines continue to increase in height, bats that migrate or forage at higher altitudes may be at increased risk (Barclay et al . 2007). Figure 1. Partial view of the Mountaineer Wind Energy Center, Tucker County, WV, located along a forested ridge top, where large numbers of bats have been killed


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 86 Are bats a ttracted to sites that provide rich foraging habitats? Modifications of landscapes during installation of wind energy facilities, including the construction of roads and power line corridors, and removal of trees to create clearings (usually 0.5 2.0 ha) a round each turbine site may create favorable conditions for the aerial insects upon which most insectivorous bats feed (Grindal and Brigham 1998; Hensen 2004). Thus, bats that migrate, commute, or forage along linear landscapes (Limpens and Kapteyn 1991; V erboom and Spoelstra 1999; Hensen 2004; Menzel et al . 2005) may be at increased risk of encountering and being killed by wind turbines. Are bats attracted to the sounds produced by wind turbines? Some bat species are known to orient toward distant audible sounds (Buchler and Childs 1981), so it is possible that they are attracted to the swishing sounds produced by the rotating blades. Alternatively, bats may become acoustically disoriented upon encountering these structures during migration or feeding. Bat s may also be attracted to the ultrasonic noise produced by turbines (Schmidt and Jermann 1986). Observations using thermal infrared imaging of flight activity of bats at wind energy facilities suggest that they do fly (and feed) in close proximity to wind turbines (Ahlén 2003; Horn et al . 2007; Figure 3). What other factors might contribute to bat fatalities? Wind turbines are also known to produce complex electromagnetic fields in the vicinity of nacelles. Given that some bats have receptors that are sen sitive to magnetic fields (Buchler and Wasilewski 1985; Holland et al . 2006), interference with perception in these receptors may increase the risk of being killed by rotating turbine blades. Bats flying in the vicinity of turbines may also become trapped in blade tip vortices (Figure 4) and experience rapid decompression due to changes in atmospheric pressure as the turbine blades rotate downward. Some bats killed at wind turbines have shown no sign of external injury, but evidence of internal tissue damag e is co nsistent with decompression (Du rr and Bach 2004; Hensen 2004). Additionally, some flying insects are reportedly attracted to the heat produced by nacelles (Ahlén 2003; Hensen 2004). Preliminary evidence suggests that bats are not attracted to the li ghting attached to wind turbines (Arnett 2005; Kerlinger et al . 2006; Horn et al . in press). Do some weather conditions place bats at increased risk of being killed by wind turbines? Preliminary observations suggest an association between bat fatalities a nd thermal inversions following storm fronts or during low cloud cover that force the animals to fly at low altitudes (Dü rr and Bach 2004; Arnett 2005). Thermal inversions create cool, foggy conditions in valleys, with warmer air masses rising to ridget op s. If both insects and bats respond to these conditions by concentrating their activities along ridge tops instead of at lower altitudes, their risk of being struck by the moving turbine blades would increase (Dü rr and Bach Figure 2 . The three species of migratory tree bats most frequently killed at wind turbine facilities in North America. (a) hoary bat ( Lasiurus cinereus ), (b) reastern red bat ( L. bo realis ), and (c) silver haireed bat ( Lasionyctyeris noctivagans ).


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 87 2004). Interestingly, the highes t bat fatalities occur on nights when wind speed is low (< 6 m s 1 ), which is when aerial insects are most active (Ahlén 2003; Fiedler 2004; Hensen 2004; Arnett 2005). Are bats at risk because they are unable to acoustically detect the moving rotor blades ? Current evidence is inconclusive as to whether bats echolocate during migration, independent of time spent searching for and capturing insects. Bats less likely to make long distant migrations in North America (e . g ., members of the genera Myotis, Eptesic us, Perimyotis ) and others that engage in long distance migrations (e . g ., Lasiurus, Lasionycteris, Tadarida ) typically rely on echolocation to capture aerial insects and to avoid objects in their flight paths. However, for most bat species, echolocation is ineffective at distances greater than 10 m (Fenton 2004), so bats foraging in the vicinity of wind turbines may miscalculate rotor velocity or fail to detect the large, rapidly moving turbine blades (Ahlén 2003; Bach and Rachmel 2004; Dü rr and Bach 2004). Given the speed at which the tips of turbine blades rotate, even in relatively low wind conditions, some bats may not be able to detect blades soon enough to avoid being struck as they navigate. Projected cumulative fatalities We have projected cumulati ve fatalities of bats at wind energy facilities for the Mid Atlantic Highlands using data on current fatality rates (Table 1) and projections of installed capacity for wind energy facilities in the Highlands for the year 2020 (see WebTable 2 for supporting data, assumptions, and calculations). Projections of installed capacity range from 2158 MW (based on the National Renewable Energy Laboratory [NREL] WinDS model [nd]) to 3856 MW (based on the PJM electricity grid operator interconnection queue; see PJM [2 006]). Although the estimated number of bat fatalities reported for each study (WebTable 1) were not consistently corrected for search efficiency or for potential bias associated with carcass removal by scavengers, we have nonetheless used these estimates to project cumulative impacts on bats because they are the only fatality rates available for bats in this region. In making our projections of cumulative fatalities, we have assumed that: (1) current variation in fatality rates is representative of the M id Atlantic Highlands, (2) future changes in design or placement of turbines (e . g . more and larger installed turbines) will not cause deviations from current fatality estimates, (3) abundance of affected bat species will not decrease due to turbine related fatalities or other factors (e . g ., habitat loss), and (4) projections of cumulative fatalities for other geographic regions differ from those in the Mid Atlantic Highlands. The projected number of annual fatalities in the year 2020 (rounded to the neare st 500) range from 33,000 to 62,000 Model, and 59,000 to 111, 000 bats based on the PJM grid operator interconnection queue. For the three migratory, tree roosting species from the Mid Atlantic Highlands, the projected cumulative fatalities in the year 2020 based on the WinDS model and PJM grid operator queue, respectively, would include 9500 to 32,000 hoary bats, 11, 500 to 38, 000 eastern red bats, and 1500 to 6 000 silver haired bats. Given the uncertainty in estimated installed wind turbine capacity for the Mid Atlantic Highlands and existing data on bat fatalities reported for this region, the above projections of cumulative fatalities should be considered provisional and thus viewed as hypotheses to be tested as impr oved estimates (or enumerations) of installed capacity and additional data on bat life histories and fatalities become available for this region. Nonetheless, these provisional projections suggest substantial fatality rates in the future. At this time, we have avoided making projections of cumulative fatalities for the entire period from 2006 2020, because of uncertainty with respect to population sizes and the demographics of bat species being killed in this region. Figure 3 . Thermal infrared image of a modern wind turbine rotor, showing the trajectory of a bat that was struck by a moving blade (lover left)


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 88 If these and other species specific pr ojections are realized for the Mid Atlantic Highlands, there may be a substantial impact on both migratory and local bat populations. Migratory tree roosting species are of particular concern because these bats have experienced the highest fatality rates a t wind energy facilities in North America. Risk assessments of ecological impacts typically require knowledge of baseline population estimates and demographics (Munns 2006). However, virtually no such data exist for any foliage roosting species (Carter et al . 2003; et al . 2003), on either regional or continental scales, that would make it possible to conduct a meaningful risk assessment. However, given the limitations noted above, the projected numbers of bat fatalities in the Mid Atlantic Highlands are very troubling. Our current knowledge and the projected future devel opment of wind energy facilities in the US suggest the potential for a substantial population impact to bats. For example, it is unlikely that the eastern red bat ( Lasiurus borealis ) could sustain cumulative fatality rates associated with wind energy development as projected, given that this species already appears to be in decline throughout much of its range (Whitaker et al. 2002; Carter et al . 2003; Winhold and Kurta 2006). There are major gaps in knowledge regarding the timing, magnitude, and patterns of bat migration, and the underlying evolutionary forces that have shaped this seasonal behavior (Fleming and Eby 2003). When lack of knowledge is combined with the fact that bats ge nerally have low reproductive rates (Barclay and Harder 2003), significant cumulative impacts of wind energy development on bat populations are likely. Much of the existing data on bat fatalities at wind energy facilities are based on monitoring studies designed primarily for the detection and estimation of bird fatalities. Results from these studies vary considerably with respect to geographic location, landscape conditions, search frequency, season of monitoring, and potential biases based on searcher e fficiency and carcass removal by scavengers. In addition, search intervals have ranged from 1 to 28 days (WebTable 1). Because some studies have shown that bats can be scavenged within hours of being killed, there is considerable uncertainty in reported fa tality estimates when search intervals longer than 24 hrs are used (Fiedler et al . 2007; Arnett et al . in press). Moreover, because only six monitoring studies have routinely used bat carcasses to correct for observer bias, the number of reported fataliti es provides, at best, a minimum estimate (WebTable 1). Research needs The unexpectedly large number of migratory tree bats being killed by wind turbines and the projected cumulative fatalities in the Mid Atlantic Highlands should be a wake up call for tho se who promote wind energy as being Uncertainties with respect to the projected fatalities, as noted above, invite comprehensive, multi year surveys and hypothesis based research to advance our understanding of where, w hen, how, and why bats are killed at wind energy facilities (Panel 1). Research is needed to develop solutions at existing facilities and to aid in assessing risk at proposed facility sites, particularly in landscapes where high bat fatalities have been re ported and in regions where little is known about the migratory and foraging habits of bats. To advance our knowledge about the causes of bat fatalities at wind energy facilities and to help guide the establishment of mitigating solutions, we propose the following research directions: and post construction monitoring protocols to ensure comparable results Figure 4 . Blade tip vortices created by mo ving rotor blades in a wind tunnel illustrate the swirling wake that trails downwind from an operating turbine.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 89 across different sites. season (April November in the continental US, for example), multi year pre an d post construction monitoring studies to assess species composition, species abundance, local population variability, and temporal and spatial patterns of bat activity at facilities that encompass diverse landscapes. and post construction s tudies that simultaneously employ different methods and tools (e.g., mist netting, horizontal and vertical radar, NEXRAD [WSR 88D] Doppler radar, thermal infrared imaging, radio telemetry, and acoustic monitoring) to improve understanding of bat activity, migration, nightly dispersal patterns, and interactions with moving turbine blades at different wind speeds. , regional , and continental scale population estimates of North American bat species. In particular, use of molecular methods to es timate effective population size of species most at risk should be a high priority. migration with respect to topography and land cover. fatality risks and the relationship between fatalities and bat demography at local, regional, and continental scales. wind energy facilities to evaluate how variations in weather and operating conditions of turbines a ffect bat activity and fatalities. Variables to be evaluated should include air temperature, wind speed and direction, cloud cover, moon phase, barometric pressure, precipitation, and turbine operating status such as rotation rate and cut in speeds. tify effects of wind turbine design on bat fatalities with respect to height and rotor diameter, base and tip height of rotor swept areas, distance between adjacent turbine rotor swept areas, and the scale (size) of wind power facilities. s of feathered (i.e., turbine blades pitched parallel to the wind, making them essentially stationary) versus not feathered (ie turbine blades pitched angularly to the wind, causing rotation) turbines at different wind speeds and at multiple sites, especia lly during high risk, migratory periods. bats to turbines (e.g., sound emissions, lighting, blade movement, prey availability, potential roosting sites). dels, with appropriate confidence intervals, on local, regional, and continental scales to evaluate impacts of wind energy development on bat populations. conditions and under different operating conditions a nd turbine characteristics at multiple sites. A call for full cooperation and research support from the wind industry As part of the permitting process, owners and developers should be required to provide full access to proposed and existing wind energy f acilities and to fund research and monitoring studies by qualified researchers. Research and monitoring protocols should be designed and conducted to ensure unbiased data collection and should be held to the highest peer review and legal standards. Panel 1 . Hypotheses for bat fatalities at wind energy facilities We propose 11 hypotheses to explain where, when, how, and why insectivorous bats are killed at wind energy facilities. These hypotheses are not mutually exclusive, given that several causes may act synergistically to cause fatalities. Nevertheless, testing these and other hypotheses promises to provide science based answers to inform researchers, developers, decision makers, and other stakeholders of the observed and projected impacts of wind energy development on bat populations. 1. Linear corridor hypothesis . Wind energy facilities constructed along forested ridge tops create clearings with linear landscapes that are attractive to bats. 2. Roost attraction hypothesis . Wind turbines attract bats bec ause they are perceived as potential roosts. 3. Landscape attraction hypothesis . Bats feed on insects that are attracted to the altered landscapes that commonly surround wind turbines. 4. Low wind velocity hypothesis . Fatalities of feeding and migrating ba ts are highest during periods of low wind velocity. 5. Heat attraction hypothesis . Flying insects upon which bats feed are attracted to the heat produced by nacelles of wind turbines. 6. Acoustic attraction hypothesis . Bats are attracted to audible and/or ultrasonic sound produced by wind turbines. 7. Visual attraction hypothesis . Nocturnal insects are visually attracted to wind turbines. 8. Echolocation failure hypothesis . Bats cannot acoustically detect moving turbine blades or miscalculate rotor velocity . 9. Electromagnetic field disorientation hypothesis . Wind turbines produce complex electromagnetic fields, causing bats to become disoriented. 10. Decompression hypothesis . Rapid pressure changes cause internal injuries and/or disorient bats while foragin g or migrating in proximity to wind turbines. 11. Thermal inversion hypothesis . Thermal inversions create dense fog in cool valleys, concentrating both bats and insects on ridge tops.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 90 Conclusions To date, bat fatalities reported in the US have been highes t at wind energy facilities along forested ridge tops in the East. While the lowest fatality rates have been observed in western states, few of these studies were designed to monitor bat fatalities, and thus may represent substantial underestimates. The hi ghest fatality rate for bats (41.6 bat fatalities MW 1 yr 1 ) was reported at the Buffalo Mountain Wind Energy Center, TN, where estimates were consistently corrected for both search efficiency and scavenging. A recent study conducted at wind energy faciliti es in an agricultural region in southwestern Alberta, Canada, unexpectedly found fatality rates comparable to those observed in some forested ridge tops in the eastern US. Given that previous monitoring studies in western agricultural and grassland regions reported relatively low fatality rates of bats, high fatality rates in regions with similar landscapes should receive increased attention. High fatality rates can also be expected at wind energy facilities located in the southwestern US, where, to date, n o monitoring studies have been conducted. Future research should focus on regions and at sites with the greatest potential for adverse effects. Improved documentation, with emphasis on evaluation of causes and cumulative impacts, should be a high priority . There is an urgent need to estimate population sizes of bat species most at risk, especially migrating, tree roosting species. Moreover, additional data are needed for assessing fatalities caused by other human activities (e . g . agricultural pesticides, h eavy metals released from the burning of fossil towers) to place impacts of wind energy development on bats into a broader context. However, these latter studies should not take priority over research to find solutions for fatalities caused by wind turbine s. An important challenge for policy makers is to ensure that owners and developers of wind energy and other energy generating facilities are required, as part of the permitting process, to fund qualified research designed to assess impacts of these facili ties on bats and other wildlife. Results of scientifically sound research and monitoring studies are needed to inform policy makers during the siting, permitting, and operation of renewable energy sources. Although bat fatalities at wind turbines have bee n reported at nearly every wind energy facility where post construction surveys have been conducted, few of these studies were designed to estimate bat fatalities and only a few included a full season or more of monitoring. Rigorous protocols should inclu de reliable estimates of searcher efficiency and scavenger removal to correct fatality estimates for potential biases. Future development of wind energy facilities, and expected impacts on bats, depend upon complex interactions among economic factors, tec hnological development, regulatory changes, political forces, and other factors that cannot be easily or accurately predicted at this time. Our preliminary projections of cumulative fatalities of bats for the Mid Atlantic Highlands are likely to be unreali stically low, especially as larger and increasing numbers of wind turbines are installed. Reliable data on bat fatalities and estimates of demographic and effective population sizes for species at risk are needed from all regions of North America, to fully understand the continental scale impacts of wind energy development. Until then, current and projected cumulative fatalities should provide an important wake up call to developers and decision makers. Additional monitoring and hypothesis based research i s needed to address a growing concern of national and international importance. Acknowledgements This paper evolved from workshops sponsored by the US Fish and Wildlife Service, Bat Conservation International, National Renewable Energy Laboratory, Nationa l Wind Coordinating Committee, Resolve, Inc, American Wind Energy Association, US Department of Energy, and the states of Colorado, Ohio, and New York. Each author made one or more presentations at these workshops and benefited from discussions with others in attendance (see WebPanel 1 for a list of these workshops and their sponsors). We thank D Boone and R Webb for providing references on assessing installed capacity of wind energy facilities in the Mid Atlantic Highlands, and D Boone, C Cleveland, P Crya n, and A Manville for their suggestions on earlier versions of this manuscript. References Ahlén I. 2003. Wind turbines and bats: a pilot study [in Swedish]. Report to the Swedish National Energy Administration. Eskilstuna, Sweden: Swedish National Energy Commission [English translation by I Ahlén]. Dnr 5210P 2002 00473, O nr P20272 1. Anderson R, Morrison M, Sinclair K, and Strickland D. 1999. Studying wind energy/bird interactions: a guidance document. Metrics and methods for determining or monitoring po tential impacts on birds at existing and proposed wind energy sites.


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Untersuchungen zu möglichen betriebsbedingten Auswirkungen von Windkraftanlagen auf Fledermäuse im Regierungsbezirk Freiburg. R egierungspräsidium Freiburg Referat 56, Naturschutz und Landschaftspflege, Stiftung Naturschutzfonds Baden Wu rttemberg (Projekt 0410 L). www.rp.baden fledermaeuse.pdf. Viewed 11 Jun 2006. Buchler ER and Childs SB. 1981. Orientation to distant sounds by foraging big brown bats ( Eptesicus fuscus ). Anim Behav 29 : 428 32. Buchler ER and Wasilewski PJ. 1985. Magnetic remanence in bats. In: Kirschvink JL, Jones DS, and MacFadden BJ (Eds). Magnetite biominer alization and magnetoreception in organisms: a new biomagnetism. New York, NY: Plenum Press. Carter TC, Menzel MA, and Saugey DA. 2003. Population trends of solitary foliage Bogan MA (Eds). Monitoring trends in bat populati ons of the United States and territories: problems and prospects. US Geological Survey, Biological Resources Discipline, Information and Technology Report. Springfield, VA: National Information Services. USGS/BRD/ITR 2003 003. Cleveland CJ, Frank JD, Feder ico P, et al . 2006. The economic value of pest control services provided by the Brazilian free tailed bat in south central Texas. Front Ecol Environ 4 : 238 43. Cryan PM. 2003. Seasonal distribution of migratory tree bats ( Lasiurus and Lasionycteris ) in Nor th America. J Mammal 84 : 579 93. Cryan PM and Brown AC. Does the migration of hoary bats past a remote island offer clues toward the problem of bat fatalities at wind turbines? Biol Conserv . In press. Dü rr T and Bach L. 2004. Bat deaths and wind turbines: a review of current knowledge and of information available in the database for Germany. Brem Beitr Naturk Naturs 7 : 253 64. EIA (Energy Information Administration). 2006. Annual energy outlook 2006 with projections to 2030. oiaf/aeo. Viewe d 20 Jun 2006. DOE/EIA 0383(2006). Erickson WP, Johnson GD, Strickland MD, and Kronner K. 2000. Avian and bat mortality associated with the Vansycle Wind Project, Umatilla County, Oregon 1999 study year. Final report. Prepared for Umatilla County Departmen t of Resource Services and Development, Pendleton, OR. Cheyenne, WY: Western Ecosystems Technology Inc. www.west reports/vansyclereportnet.pdf. Viewed 11 Jun 2007. Erickson WP, Jeffrey J, Kronner K, and Bay K. 2003a. Stateline Wind Project wildlif e monitoring annual report, results for the period July 2001 December 2002. Technical report prepared for FPL Energy, the Oregon Office of Energy, and the Stateline Technical Advisory Committee. Cheyenne, WY: Western EcoSystems Technology Inc. www.west inc .com/reports/swp_ final_dec04.pdf. Viewed 11 Jun 2007. Erickson WP, Gritski PB, and Kronner K. 2003b. Nine Canyon Wind Power Project avian and bat monitoring annual report. Technical report submitted to Energy Northwest and the Nine Canyon Technical Adviso ry Committee. Cheyenne, WY: Western EcoSystems Technology Inc. www.west reports/nine_canyon_monitoring_final.pdf. Viewed 11 Jun 2007. Fenton MB. 2004. Bat natural history and echolocation. In: Brigham RM, Kalko EKV, Jones G, et al . (Eds). Bat echo location research: tools, techniques and analysis. Austin, TX: Bat Conservation International. Fiedler JK. 2004. Assessment of bat mortality and activity at Buffalo Mountain Windfarm, eastern Tennessee (MS thesis). Knoxville, TN: University of Tennessee. F iedler JK, Henry TH, Nicholson CP, et al . 2007. Results of bat and bird mortality monitoring at the expanded Buffalo Mountain windfarm, 2005. Knoxville, TN: Tennessee Valley Authority.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 92 Fleming TH and Eby P. 2003. Ecology of bat migration. In: Kunz TH and F enton MB (Eds). Bat ecology. Chicago, IL: University of Chicago Press. GAO (US Government Accountability Office). 2005. Wind power: impacts on wildlife and government responsibilities for regulating development and protecting wildlife. Washington, DC: US G overnment Accountability Office. new.items/d05906.pdf. Viewed 11 Jun 2007. Grindal SD and Brigham RM. 1998. Short term effects of smallscale habitat disturbance on activity by insectivorous bats. J Wildlife Manage 62 : 996 1003. Gruver JC. 2002 . Assessment of bat community structure and roosting habitat preferences for the hoary bat ( Lasiurus cinereus ) near Foote Creek Rim, Wyoming (MS thesis). Laramie, WY: University of Wyoming. Holland RA, Thorup K, Vonhof M, et al . 2006. Navigation: bat orien Nature 444 : 702. Hoover SL and Morrison ML. 2005. Behavior of red tailed hawks in a wind turbine development. J Wildlife Manage 69 : 150 59. Horn JW, Arnett EB, and Kunz TH. Behavioral responses of bats to operating win d turbines. J Wildlife Manage . In press. Howe RW, Evans W, and Wolf AT. 2002. Effects of wind turbines on birds and bats in northeastern Wisconsin. Madison, WI: Wisconsin Public Service Corporation. Jain A. 2005. Bird and bat behavior and mortality at a n orthern Iowa windfarm (MS thesis). Ames, IA: Iowa State University. Johnson GD. 2005. A review of bat mortality at wind energy developments in the United States. Bat Res News 46 : 45 49 . Johnson GD, Erickson WP, and White J. 2003a. Avian and bat mortality a t the Klondike, Oregon Phase I Wind Plant, Sherman County, Oregon. Technical Report prepared for Northwestern Wind Power. Cheyenne, WY: Western EcoSystems Technology Inc. www.west php. Viewed 11 Jun 2007. Johnson GD, Erickson WP, Stri ckland MD, et al . 2003b. Mortality of bats at a large scale wind power development at Buffalo Ridge, Minnesota. Am Midl Nat 150 : 332 42. Johnson GD, Perlik MK, Erickson WP, and Strickland MD. 2004. Bat activity, composition and collision mortality at a lar ge wind plant in Minnesota. Wildl Soc B 32 : 1278 88. Keith G, Biewald B, Sommer A, et al . 2003. Estimating the emission reduction benefits of renewable electricity and energy efficiency in North America: experience and methods. Prepared for the Commission for Environmental Cooperation. September 22, 2003. www.synapse SynapseReport.2003 09.CEC.Emission Reduction Benefits Renewables and EE Estimates.03 18.pdf. Viewed 11 Jun 2007. Kerlinger P, Curry R, Culp L, et al . 2006. Post construct ion avian and bat fatality monitoring study for the High Winds Wind Power Project, Solano County, California: two year report. McLean, NJ: Curry and Kerlinger LLC. Kerns J and Kerlinger P. 2004. A study of bird and bat collision fatalities at the Mountaine er Wind Energy Center, Tucker County, West Virginia. FPL Energy and Mountaineer Wind Energy Center Technical Review Committee. Cape May, NJ: Curry and Kerlinger LLC. FinalAvianRpt3 15 04PKJK.pdf. Viewed 11 Jun 2007. Kerns J, Erickson WP, and Arnett EB. 2005. Bat and bird fatality at wind energy facilities in Pennsylvania and West Virginia. In: Arnett EB (Ed). Relationships between bats and wind turbines in Pennsylvania and West Virginia: an assessment of bat fatality search protocols, patterns of fatality, and behavioral interactions with wind turbines. A final report submitted to the Bats and Wind Energy Cooperative. Austin, TX: Bat Conservation International. pdf. Viewed 11 J un 2007. Kunz TH. 2004. Foraging habits of North American insectivorous bats. In: Brigham RM, Kalko EKV, Jones G, et al . (Eds). Bat echolocation research: tools, techniques, and analysis. Austin, TX: Bat Conservation International. Kunz TH and Lumsden LF. 2003. Ecology of cavity and foliage roosting bats. In: Kunz TH and Fenton MB (Eds). Bat ecology. Chicago, IL: University of Chicago Press. Limpens HJGA and Kapteyn K. 1991. Bats, their behaviour and linear landscape elements. Myotis 29 : 39 48. Manville AM II. 2005. Bird strikes and electrocutions at power lines, communication towers, and wind turbines: state of the art and state of the science next steps toward mitigation. In: Ralph CJ and Rich TD (Eds). Proceedings of the 3rd International Partners in Fl ight Conference, Vol 2; 2002 March 20 24; Asilomar, CA. Albany, CA: Pacific Southwest Research Station, Forest Service. USDA Forest Service General Technical Report, PSW GTR 191. psw_gtr191/Asilomar. Viewed 11 Jun 2007. McCracken GF. 2003. Estimates of population sizes in summer colonies of Brazilian free tailed bats ( Tadarida brasiliensis Monitoring trends in bat populations of the United States and territories: problems and pros pects. US Geological Survey, Biological Resources Discipline, Information and Technology Report. Springfield, VA: National Information Services. USGS/BRD/ITR 2003 003, Menzel JM, Menzel Jr MA, Kilgo JC, et al . 2005. Effects of habitat and foraging height o n bat activity in coastal plain of South Carolina. J Wildlife Manage 69 : 235 45. Morrison ML and Sinclair AK. 2004. Environmental impacts of wind energy technology. In: Cleveland CJ (Ed). Encyclopedia of energy, vol 6. New York, NY: Elsevier. Munns WR Jr. 2006. Assessing risks to wildlife populations from multiple stressors: overview of the problem and research needs. Ecol Soc 11 : 23. Viewed 11 Jun 2007.


BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 93 National Wind Watch Inc. 2006. Presenting the facts about industrial wind power. www.wind china catch the wind/. Viewed 11 Jun 2007. Osborn RG, Higgins KF, Dieter CD, and Usgaard RE. 1996. Bat collisions with wind turbines in southwestern Minnesota. Bat Res News 37 : 105 08. hea TJ, Bogan MA, and Ellison LE. 2003. Monitoring trends in bat populations of the United States and territories: status of the science and recommendations for the future. Wildlife Soc B 31 : 16 29. Pasqualetti M, Richter R, and Gipe P. 2004. History of wi nd energy. In: Cleveland CJ (Ed). Encyclopedia of energy, vol 6. New York, NY: Elsevier. Piorkowski M. 2006. Breeding bird habitat use and turbine collisions of birds and bats located at a wind farm in Oklahoma mixed grass prairie (MS thesis). Stillwater, OK: Oklahoma State University. Pierson ED. 1998. Tall trees, deep holes, and scarred landscapes: conservation biology of North American bats. In: Kunz TH and Racey PA (Eds). Bat biology and conservation. Washington, DC: Smithsonian Institution Press. PJM ( PJM Environmental Information Services). 2006. Wind energy applications filed for grid interconnection study within Mid Atlantic Highland Region of PJM (PA, WV, MD, DC & VA). _summary_073106.pdf. Viewed 11 Nov 2006. Schmidt U and Jermann G. 1986. The influence of acoustical interferences on echolocation in bats. Mammalia 50 : 379 89. UNEP/Eurobats. 2005. Report of the Intersessional Working Group on wind turbines and bat populations. 10th Meeting of the Advis ory Committee; 25 27 Apr 2005; Bratislava, Slovak Republic. _9_Report_IWG_WindTurbines.pdf. Viewed 11 Jun 2007. Verboom B and Spoelstra K. 1999. Effects of food abundance and wind on the use of tree lines by an i nsectivorous bat, Pipistrellus pipistrellus . Can J Zool 77 : 1393 1401. von Hensen F. 2004. Gedanken und Arbeitshypothesen zur Fledermausverträglichkeit von Windenergieanlagen. Nyctalus 9 : 427 35. Whitaker JO Jr, Brack V, and Cope JB. 2002. Are bats in Indi ana declining? P Indiana Acad Sci 111 : 95 06. NREL (National Renewable Energy Laboratory). Nd. WinDS Model. Viewed 11 Jun 2007. Winhold L and Kurta A. 2006. Are red bats ( Lasiurus borealis ) declining in southern Michigan? Bat Res News 46 : 229. Young Jr DP, Erickson WP, Good RE, et al . 2003. Avian and bat mortality associated with the initial phase of the Foote Creek Rim Windpower Project, Carbon County, Wyoming: November 1998 June 2003. Cheyenne, WY: Western EcoSystems Technolo gy Inc. Technical Report Prepared for Pacificorp Inc, SeaWest Windpower Inc, and Bureau of Land Management, Rawlings District Office, Rawlings, WY. www.west Viewed 20 Apr 2006. WebPanel 1. Additional acknowledgements This paper evolved as an outgrowth of several state, regional, and national wind energy and wildlife workshops, including: Bats and wind power generation technical workshop (Juno Beach, FL; 19 20 February 2004; sponsored by the US Fish and Wildlife Servi ce [USFWS], Bat Conservation International, National Renewable Energy Laboratory, and American Wind Energy Association) Wind energy and birds/bats workshop: understanding and resolving bird and bat impacts (Washington, DC; 18 19 May 2004; sponsored by th e National Wind Coordinating Committee [NWCC]) Research meeting V: onshore wildlife interactions with wind development (Lansdowne, VA; 3 4 Nov 2004; sponsored by NWCC) Wind power and wildlife in Colorado (Fort Collins,CO;23 25 Jan 2006; sponsored by th e Colorado Department of Natural Resources) Toward wildlife friendly wind power: a focus on the Great Lakes (Toledo, OH; 27 29 Jun 2006; sponsored by US Environmental Protection Agency, USFWS Great Lakes Basin Ecosystem Team, Illinois Natural History Sur vey, and US Geological Survey) New York wind/wildlife technical workshop (Albany, NY; 2 3 Aug 2006; sponsored by the New York State Energy Research and Development Authority, and New York Department of Environmental Conservation)


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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 96 Bat White Nose Sy ndrome: An Emerging Fungal Pathogen? David S. Blehert, 1 * Alan C. Hicks, 2 Melissa Behr, 3 1 Brenda M. Berlowski Zier, 1 Elizabeth L. Buckles, 4 Jeremy T. H. Coleman, 5 Scott R. Darling, 6 Andrea Gargas, 7 Robyn Niver, 5 Joseph C. Okoniewski, 2 Rob ert J. Rudd, 3 Ward B. Stone 2 Science Vol. 323: 227 (9 January 2009) 1 National Wildlife Health Center, U.S. Geological Survey (USGS), 6006 Schroeder Road,Madison,WI 53711, USA. 2 New York Department of Environmental Conservation, 625 Broadway, Albany, NY 1 2233, USA. 3 New York Department of Health, Post Office Box 22002, Albany, NY 12201, USA. 4 Cornell University, VRT T6008, Ithaca, NY 14853, USA. 5 U.S. Fish and Wildlife Service, 3817 Luker Road, Cortland, NY 13045, USA. 6 Vermont Fish and Wildlife Department , 271 North Main Street, Rutland, VT 05701, USA. 7 Symbiology Limited Liability Corporation, Middleton, WI 53562, USA. *To whom correspondence should be addressed. E mail: asterday Lane, Madison, WI 53706, USA. T he first evidence of bat white nose syndrome (WNS) was documented in a photograph taken at Howes Cave, 52 km west of Albany, New York, on 16 February 2006. Since emerging in the northeastern United States, WNS has been confirmed by gross and histologic examinations of bats at 33 sites in Connecticut, Massachusetts, New York, and Vermont (fig. S1). Current bat population surveys suggest a 2 year population decline in excess of 75% [see supporting on line material (SO M) text for further details]. WNS has been characterized as a condition of hibernating bats and was named for the visually strikingwhite fungal growth on muzzles, ears, and/ or wing membranes of affected bats (Fig. 1A). Detailed postmortem evaluations wer e completed for 97 little brown myotis ( Myotis lucifugus ; Mylu), nine northern long eared myotis ( M. septentrionalis ; Myse), five big brown bats ( Eptesicus fuscus ; Epfu), three tricolored bats ( Perimyotis subflavus ; Pesu), and three unidentified bats from 18 sites within the WNS affected region. Distinct cutaneous fungal infection was observed in histologic sections from 105 of the 117 necropsied bats [91 Mylu (94%), eight Myse (89%), zero Epfu (0%), three Pesu (100%), and three unidentified (100%)]. Fungal hyphae replaced hair follicles and associated sebaceous and sweat glands, breaching the basement membrane and invading regional tissue. Hyphae also eroded the epidermis of ears and wings (Fig. 1B). Additionally, 69 of the 105 bats [62 Mylu (64%), six Myse (67%), zero Epfu (0%), one Pesu (33%), and zero unidentified (0%)] with cutaneous fungal infection had little or no identifiable fat reserves, crucial for successful hibernation [see SOM text for additional mortality investigation details]. A fungus with a previously undescribed morphology was isolated from 10 bats (table S1) with histologic evidence of WNS associated cutaneous fungal infection. These bats were collected between 1 February and 1 April 2008 from all states within the confirmed WNS affected region (fig. S1). The distinctive curved conidia (Fig. 1C) of the isolates were identical to conidia scraped directly from the muzzles of WNS affected little brown myotis collected at Graphite Mine (New York) and to conidia observed histologically on the surface of infected bat skin (Fig. 1B, inset). Isolates were initially cultured at 3°C, grew optimally between 5°C and 10°C, but grew marginally above 15°C. The upper growth limit was about 20°C. Temperatures in WNS affected hibernacula seasonally range be tween 2° and 14°C, permitting year round growth and reservoir maintenance of the psychrophilic fungus. Phylogenetic analysis of the identical internal transcribed spacer region (fig. S2) and small subunit (fig. S3) ribosomal RNA gene sequences from the 10 psychrophilic fungal isolates placed them within the inoperculate ascomycetes (Order Helotiales) near representatives of the anamorphic genus Geomyces (teleomorph Pseudogymnoascus) (1). In contrast to the genetic data, morphology of the psychrophilic fung al isolates differed from that known for Geomyces species. The bat isolates produced single, curved conidia (Fig. 1C)morphologically distinct from clavate and arthroconidia characteristic of Geomyces (2). Species of Geomyces are terrestrial saprophytes tha t grow at cold temperatures (3). Placement of the WNS fungal isolates within Geomyces, members of which colonize the skin of animals in cold climates (4), is consistent with properties predicted for a causative agent of WNS associated cutaneous infection. Worldwide, bats play critical ecological roles in insect

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 97 control, plant pollination, and seed dissemination (5), and the decline of North American bat populations would likely have far reaching ecological consequences. Parallels can be drawn between the threat posed by WNS and that from chytridiomycosis, a lethal fungal skin infection that has recently caused precipitous global amphibian population declines (6). A comprehensive understanding of the etiology, ecology, and epidemiology of WNS is essential t o develop a strategy to manage this current devastating threat to bats of the northeastern United States. References 1. A. V. Rice, R. S. Currah, Mycologia 98, 307 (2006). 2. L. Sigler, J. W. Carmichael, Mycotaxon 4, 349 (1976). 3. S. M. Duncan et al., Antarct. Sci. 10.1017/ S0954102008001314 (2008). 4. W. A. Marshall, Microb. Ecol. 36, 212 (1998). 5. T. H. Kunz, M. B. Fenton, Bat Ecology (Univ. Chicago Press, Chicago, 2003). 6. L. F. Skerratt et al., EcoHealth 4, 125 (2007). Fig. 1 . (A) A little brown bat, found in Howes Cave on 6 January 2008, exhibits white fungal growth on its muzzle, ears, and wings. (B) Fungal invasion of bat skin (periodic acid Schiff stain). Hyphae cover the epidermis (thick arrow); fill hair follicles, sebaceous glands, and sweat glands (thin arrows); breach the basement membrane; and invade regional tissue (arrowhead). (Inset) Curved conidia associated with the epidermis. (C) WNS associated Geomyces spp. isolate stained with lactophenol cotton blue. Scale bars indicate 10 mm.

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 98 Supporting Online Materi al for Bat White Nose Syndrome: An Emerging Fungal Pathogen? David S. Blehert,* Alan C. Hicks, Melissa Behr, Carol U. Meteyer, Brenda M. Berlowski Zier, Elizabeth L. Buckles, Jeremy T. H. Coleman, Scott R. Darling, Andrea Gargas, Robyn Niver, Joseph C. Oko niewski, Robert J. Rudd, Ward B. Stone *To whom correspondence should be addressed. E mail: Published 30 October 2008 on Science Express DOI: 10.1126/science.1163874 Abstract: White nose syndrome (WNS) is a condition associated with an unprecedented bat mortality event in the northeastern United States. Since the winter of 2006 2007 bat declines exceeding 75% have been observed at surveyed hibernacula. Affected bats often present with visually stri king white fungal growth on their muzzles, ears, and/or wing membranes. Direct microscopy and culture analyses demonstrated that the skin of WNS affected bats is colonized by a psychrophilic fungus that is phylogenetically related to Geomyces spp. , but wit h a conidial morphology distinct from characterized members of this genus. This report characterizes the cutaneous fungal infection associated with WNS. Materials and Methods: Finite annual population growth rates (R) were estimated for the two caves tha t had at least three surveys since 2005, Hailes (R = 0.47) and Schoharie (R = 0.17). These corresponded with two year population declines of 78% and 97%, respectively. We assumed the geometric population model N t+I = N t R i , where N t is the population at tim e t, and R is the finite annual growth rate. We estimated log(R) for each cave using the semilog regression model log(N t+i ) = log(N t ) + log(R)i, and obtained the estimate of R as R = exp(log(R)). The estimated two year decline was obtained as 100(1 R 2 ). Al though we assumed a model of constant change, the semilog plots suggest an accelerating decline (Fig. S4). DNA was extracted from each fungal isolate using microLYSIS PLUS reagent (The Gel Company, San i nstructions. rRNA gene internal transcribed spacer (ITS) region DNA (ITS1, 5.8S, and ITS2) was PCR amplified using primers ITS4 and ITS5 (S1) and ExTaq proof reading DNA polymerase (Takara Mirus Bio, Madison, Wisconsin). Cycling parameters were an initial 2 min denaturation at 98°C followed by 30 cycles of denaturation at 98°C for 10 s, annealing at 50°C for 30 s, and extension at 72°C for 1 min, with a final extension at 72°C for 7 min. rRNA gene small subunit (SSU) DNA was PCR amplified using primers nu S SU 0021 and nu SSU 1750 the extension time was increased to 2 min. Sequencing primers were PCR primers with the addition of nu SSU 0402 nu SSU 1150 SSU 0497 SSU 1184 . PCR products were submitted to the University of Wisconsin Madison Biotechnology Center DNA Sequencing Facility for direct, double stranded sequence determination using the BigDye Terminator v3.1 (Applied Biosystems, Foster City, California) DNA sequen cing system. Reaction products were analyzed using an Applied Biosystems 3730xl automated DNA sequencing instrument. Complementary strand sequencing reaction results were assembled and edited for accuracy using Lasergene 5.0 (DNAStar, Madison, Wisconsin). rRNA gene ITS (EU854569 EU854572, EU884920 EU884924, and FJ170115) and SSU (FJ231093 FJ231102) sequences are archived in GenBank. As the ITS and SSU sequences from each of the ten WNS fungal isolates were identical to each other, they were represented in p hylogenetic analyses by single sequences (EU854571 for ITS and FJ231093 for SSU). Although excluded from the sequences used in analysis of the ITS region, additional genetic support comes from the presence of a putative group I intron of ca 415 nt, located at small subunit position 1506 (S4) of each isolate, with 97% sequence similarity to insertions in Geomyces spp . AY345348 and AY345347. ITS and SSU sequences for comparison were selected from similar sequences archived in GenBank determined through BLAST search hits to query WNS isolate sequences, including only taxa with near complete gene sequences. Sequences were aligned visually using Se AL (v2.0a11) (S5). The ITS alignment of 537 nt for 20 taxa and the SSU alignment of 1725 nt for 18 taxa are archived in TreeBase SN3954 18967. Parsimony phylograms were determined with PAUP* (4.0b10) (S6). Reliability of nodes was assessed with Bayesian posterior probabilities calculated using MCMC (MrBayes 3.1.2) (S7, S8) using the GTR model and running four chains wit h 1,000,000 generations, sampling each 1,000 th tree and discarding as burn in all pre convergence trees; and bootstrap percentages based on 1,000 replicates in PAUP* (S4). Supporting Text: Following the emergence of WNS during the winter of 2006 2007, the number of reports of day flying bats recorded by the New York State Department of Health rabies laboratory for Schoharie County peaked in mid March, 2007 at approximately 10

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 99 times the previous 25 year record high. This trend continued throughout the winte r of 2007 2008 for Schoharie county and expanded to include Ulster County. All bats tested negative for rabies. Additional bacteriological and virological analyses of internal organs from WNS suspect bats revealed no known pathogens. Disease causing parasi tes were not found following examination of intestinal tracts. No consistent, significant lesions were observed upon gross or microscopic examination of internal organs from bats with the WNS associated cutaneous fungal infection. Post mortem evaluations w ere also completed for five little brown myotis from an unaffected mine in Wisconsin and eight little brown myotis from an unaffected cave in Kentucky, and no lesions were seen in their skin or internal organs. Fig. S1. Hibernacula locations, including th e index site Howes Cave, confirmed by survey to be positive for WNS. Fungal isolates from which ITS and SSU sequence data were generated were cultured from bats collected at sites designated with plus signs. Fig. S2. One of 13 equally parsimonious trees f or the ITS alignment (Length = 286, CI = 0.734, RI = 0.805). GenBank accession numbers precede taxa names, and the WNS fungal isolate sequence is indicated in bold with a bat image. Branch length is relative to the number of substitutions per site. Posteri or probability values are shown above each supported node, and bootstrap percentages are shown below supported nodes. Fig. S3. One of 5 equally parsimonius trees for the SSU alignment (Length = 194, CI = 0.825, RI= 0.807). GenBank accession numbers prece de taxa names, and the WNS fungal isolate sequence is indicated in bold with a bat image. Branch length is relative to the number of substitutions per site. Posterior probability values are shown above each supported node, and bootstrap percentages are sho wn below supported nodes. Fig. S4. Bat population trends for Hailes Cave and Schoharie Caverns. Supplemental References: S1. T. J. White, T. D. Bruns, S. B. Lee, J. W. Taylor, in PCR protocols: a guide to methods and applications , M. A. Innis, D. H. Gelf and, J. J. Sninsky, T. J. White, Eds. (Academic Press, New York, 1990), pp. 315 321. S2. A. Gargas, P. T. DePriest, Mycologia 88 , 745 (1996). S3. A. Gargas, J. W. Taylor, Mycologia 84 , 589 (1992). S4. A. Gargas, P. T. DePriest, J. W. Taylor, Mol. Biol. Evo l. 12 , 208 (1995). Al: Sequence Alignment Editor Version S6. D. L. Swofford, PAUP*. Phylogenetic analysis using parsimony (*and other methods) Version 4 (Sinauer Ass ociates, Sunderland, Massachusetts, 2002). S7. J. P. Huelsenbeck, F. Ronquist, Bioinformatics 17 , 754 (2001). S8. F. Ronquist, J. P. Huelsenbeck, Bioinformatics 19 , 1572 (2003). S9. We thank T. Kunz (Boston University), M. Friend (USGS National Wildlife He alth Center), and D. Constantine for manuscript suggestions. At the USGS National Wildlife Health Center, supporting pathology was provided by D. Green, N. Thomas, and V. Shearn Bochsler; laboratory support was contributed by H. Ip (virology), D. Berndt (m icrobiology), and M. Sterner (parasitology). Population trend analysis was conducted by D. Heisey. At Cornell University, we acknowledge the anatomic pathology and wildlife medicine faculty and staff; supporting pathology was provided by K. Hulme. We also thank A. Lowell (USFWS), C. Herzog (NYSDEC), A. Davis (NYSDOH), B. Wood (NYSDOH), and the many individuals who provided survey data and specimen collection assistance for hibernacula throughout the northeastern United States. Additional field support was p rovided by D. Redell (WI Department of Natural Resources) and T. Hemberger (KY Department for Fish and Wildlife Resources). We acknowledge Bat Conservation International for helping to bring researchers together from across North America to share data and ideas on WNS. Work reported here was supported directly by the US Geological Survey, the US Fish and Wildlife Service, the New York State Department of Environmental Conservation, and the New York State Department of Health.

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 100 Fig. S1 (top) Fig. S2 (bottom)

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 101 Fig. S3 (top) Fig. S4 (bottom)

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 104 Food Habit s of U.S. and Canadian Bat Species Adapted with permission from: Lollar, A. and B.A.S. French. 1998. Captive Care and Medical Reference for the Rehabilitation of Insectivorous Bats , 2002 (2 nd Ed.). Bat World Publications, Mineral Wells, TX. 340 pages. FA MILY MORMOOPIDAE Species Name Common Name Feeding Information and Food Habits Mormoops megalophylla faced bat Large moths FAMILY PHYLLOSTOMIDAE Species Name Common Name Feeding Information and Food Habits Artibeus jamaicensis Jamaican fr uit eating bat Fruit and nectar, including pollen and a few insects. Mexican long tongued bat Fruit, pollen, nectar, and probably insects. Lesser long nosed bat Nectar, pollen, and insects. Leptonycter is nivalis Mexican long nosed bat Nectar and pollen; including from the flowers of Agave spp. Macrotus californicus California leaf nosed bat Beetles of the families Scarabaeidae and Carabidae, grasshoppers, cicadas, noctuid moths, caterpillars, remains of sphinx moths, butterflies and dragonflies have been found beneath night roosting sites; often feeds on the ground. FAMILY VESPERTILIONIDAE Species Name Common Name Feeding Information and Food Habits Antrozous pallidus Pallid bat Ground beetles, June beetles, moths, crickets (including Jerusalem crickets) froghoppers and leafhoppers, antlions, grasshoppers, scorpions. Corynorhinus rafinesquii eared bat Moths. Corynorhinus townsendii eared bat Primarily moths; also fli es, lacewings, dung beetles and sawflies. Eptesicus fuscus Big brown bat Scrab, June beetles, spotted cucumber beetles, leaf beetles, ground beetles, termites, true bugs, leafhoppers, flying ants. Euderma maculatum Spotted bat Moths. Idionycteris phyllo tis eared bat Primarily moths (microlepidopterans), soldier beetles (Cantharidae), dung beetles (Scarabaeidae), leaf beetles (Chrysomelidae), roaches (Blattidae), and flying ants (Formicidae, including Eciton)_ Lasionycteris noctivagans Silver haired bat Moths, bugs, beetles, flies, and caddis flies. Lasiurus blossevillii Western red bat Large moths, beetles, and grasshoppers. Lasiurus borealis Eastern red bat Generalist: Moths, scarab beetles, plant hoppers, flying ants, leafhoppers, ground beetles, and assassin bugs. Lasiurus cinereus Hoary bat Primarily moths, also beetles, grasshoppers, termites, and dragonflies. Lasiurus ega Southern yellow bat § Lasiurus intermedius Northern yellow bat Leafhoppers, dragonflies, flies, diving beetles, Scotylidae beetles*, ants, and mosquitoes Lasiurus seminolus Seminole bat Moths, true bugs, flies, beetles (including Scolytids*) and ground dwelling crickets. Lasiurus xanthinus Western yellow bat § Myotis auriculus Southwestern myotis § Myotis austro riparius Southeastern myotis Diptera, Coleoptera, and other flies, including some mosquitoes. Myotis californicus Californian myotis Small moths, flies, and beetles that occur between, within, or below the vegetative canopy. Myotis ciliolabrum Western sm all footed myotis Moths, Diptera, Hemiptera, beetles, Homoptera. Myotis evotis Long eared myotis Leptdoptera, Coleoptera, Diptera, neuroptera, Hymenoptera, Hemiptera, and Homoptera (examples include a cicadellid, a chironomid, a small moth, a scarab beetl e, a dragonfly, muscoid fly, Culicid species and other aquatic insects. Myotis grisescens Gray myotis Coleoptera, Lepidoptera, Homoptera, mayflies (Epheneroptera: Ephemeridae), Trichopteria, Hemiptera. Myotis keenii §

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 105 Species Name Common Name Feeding Information and Food Habits Myotis leibii Eastern small footed myotis Flies (Anthomyiidae), bugs (Jassidae), Agallia, Piesma cinerium, minute Scarabaeidae, Staphylinidae, and ants. Myotis lucifugus Little brown myotis Flies, moths, beetles, aquatic insects (water boatman, mayflies, chironomids), moths, midges, mosquitoes, flies, beetles, plant bugs, Myotis occultus Arizona myotis Aquatic insects (probably mosquitoes and midges) Myotis septentrionalis Northern myotis Moths, beetles, and flies. Myotis sodalis Indiana myotis Lepidopter a, Coleoptera, Diptera, Trichoptera, Hymenoptera (Ichneumonidae), and Homoptera. Myotis thysanodes Fringed myotis Moths, beetles, Homoptera, Diptera Myotis velifer Cave myotis Small moths, weevils, ant lions, small beetles Myotis volans Long legged myot is Small moths, beetles, flies, Homoptera, Hemiptera Myotis yumanensis Yuma myotis Flies, moths, beetles, frog hoppers and leafhoppers, June beetles, ground beetles, midges, muscid flies, caddis flies, and crane flies. Nycticeius humeralis Evening bat Ju ne beetles, Hemiptera, flyng ants, spittle bugs, June beetles, pomace flies, and moths. Parastrellus hesperus Canyon bat Moths, small beetles, flies, caddis flies, stoneflies, leaf and stilt bugs, leafhoppers, flies, mosquitoes, ants, wasps. Perimyotis s ubflavus Tri colored bat Small beetles, small leafhoppers, ground beetles, flies, moths, and ants. FAMILY MOLOSSIDAE Species Name Common Name Feeding Information and Food Habits Eumops floridanus Florida bonneted bat § Eumops perotis Greater bonneted b at Moths, beetles, flies, crickets, grasshoppers, bees, dragonflies, leaf bugs, and cicadas. Eumops underwoodi Scarab beetles including June beetles (Scarabaeidae), short hored grasshoppers (Acrididae) including Trimerotropis pall idipennis, leafhoppers (Cicadellidae), moths (Lepidoptera), leaf beetles (Chrysomelidae), plant hoppers (Fulgoridae), and long horned beetles (Cerambycidae). Molossus molossus § Perhaps chiefly moths, beetles, and ants. Nyctinomops f emorosaccus Pocketed free tailed bat Moths, crickets, flying ants, stink bugs, frog hoppers, leafhoppers, and lacewings. Nyctinomops macrotis Big free tailed bat Primarily moths, also crickets, flying ants, stink bugs, froghoppers and leafhoppers. Tadari da brasiliensis Mexican free tailed bat Moths, flying ants, June beetles, leafhoppers, and true bugs (also midges, mosquitoes, flies, water boatmen, and brown lace Feeding information given as common names (e.g., moths, etc.), scientific classif ications (e.g., family Lepidoptera, etc.) or both, depending on the source. This table is intended only as a very general guideline. § Information not available from reference sources used. Historical records of Greater long nosed bats in Arizona refer to L. curasoae (yerbabuenae) . However, records of L. nivalis from the Peloncillo Mountains near the New Mexico/Arizona border indicate this species may occur in Arizona. . References Barbour, R.W. and W.H. Davis. 1969. Bats of America . University Press of Kentucky, Lexington, 286 pages. Bats for Insect Biocontrol in Agriculture . Monitoring the Field of Pest Management, 18(9). * Scherman, H.B. 1939. Not es on the food of some florida bats. Journal of Mammalogy 20: 103 104. Schmidly, D.J. 1991. The Bats of Texas . Texas A&M University Press, College Station, 188 pages. Additional information from personal communication with John Whitaker and from Mammalian Species accounts for the following species: Idionycteris phyllotis (#208), Lasiurus ega (#515), Myotis auriculus (#191), Myotis evotis (#329), Myotis grisescens (#510), Myotis sodalis (#163) and Eumops underwoodi (#516).

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 106 Prey Selection in a Temperate Zo ne Insectivorous Bat Community John O. Whitaker , J r .* * Department of Life Sciences, Indiana State University, Terre Haute, IN 47809, USA Journal of Mammalogy , 85(3):460 469, 2004 I determined foods eaten by bats at Prairie Creek, Vigo County, Indiana, to test the null hypothesis that insectivorous bats eat primarily whatever is available. If bats eat what is available, then all bats taken at the same time and place should eat the same foods. I collected fecal samples from 486 bats of 8 species from 1993 t hrough 1997 in a 650 ha deciduous forest in t Eptesicus fuscus and Nycticeius humeralis fed heavily on coleopterans, followed by hemipterans in E. fuscus and homopterans in N. humeralis . Lasiurus borealis fed most heavily on lepidopterans, followed by coleopterans and homop terans. fed approximately equally on homopterans, coleopterans, and dipterans. The main foods were similar for Myotis sodalis, M. lucifugus , and M. septentrionalis : dipterans 1st, followed by lepidopterans, trichopterans, and then col eopterans in M. lucifugus and by coleopterans and then lepidopterans in the other 2 species. It is clear that bats at Prairie Creek selected from among the available foods. Myotis septentrionalis , a gleaner, did not eat foods appreciably different from oth er bats in the same genus. Key words : bats, Chiroptera, food habits, Indiana It has been suggested that insectivorous bats, especially Myotis , sometimes feed on whatever insects are available at a given time and place (Belwood and Fenton 1976; Fenton and Morris 1976). Availability of insects (Fenton 1987; Kunz 1988; Whitaker 1994). Because a large and diverse community of insectivorous bats occurs at my study area at Prairie Creek, Vigo County, Indiana (Whitaker 1996), this provided an excellent opportunity to test the hypothesis that insectivorous bats simply feed on the available insect taxa: if bats eat what is available, then all bats taken at the same time and place should essentially feed on the same foods. In this st udy, I compare food habits among 8 species of bats in a single community, and between sexes and juveniles within species, to test the null hypothesis that insectivorous bats simply feed on whatever insects are available. In addition, foods of the gleaning bat Myotis septentrionalis (Brack and Whitaker 2001; Faure et al. 1993) were compared with foods eaten by other bats. M ATERIALS AND M ETHODS Ten species of bats currently exist in Indiana, and 9 of these occur at bottom lands of the Wabash River in southern Vigo County and bisects a 650 ha contiguous woodland before entering the Wabash River in Sullivan County to the south. Eight species are found at Prairie Creek throughout the warm seasons: the evening bat ( Nycticeius h umeralis ), the big brown bat ( Eptesicus fuscus ), the northern myotis ( Myotis septentrionalis ), the red bat ( Lasiurus borealis ), the little brown myotis ( Myotis lucifugus ), the eastern pipistrelle ( Pipistrellus ), the Indiana myotis ( Myotis sodalis ) , and the hoary bat ( Lasiurus cinereus ). The silver haired bat ( Lasionycteris noctivagans ) is found during spring and autumn migration. The species are listed above in approximate order of decreasing abundance (Table 1). The study area and bat fauna were m ore completely described by Whitaker (1996). I captured 881 bats of 8 of the species from 1994 through 1997 at Prairie Creek. All bats were released shortly after capture, but many plastic bags and held 10 min to collect fecal samples. I obtained fecal samples from 486 bats including all 8 species. In the laboratory, each fecal sample was examined using a 10 70x zoom dissecting microscope (Olympus America SZH, Melville, New York). The series of fecal pellets from each bat was treated as 1 sample. This was done to prevent bias from varying numbers of pellets per bat and because my experience shows that individual pellets within 1 fecal sample show much less varia tion than do samples from separate bats.

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 107 The fecal pellets from each bat were teased apart in a petri dish containing a small amount of alcohol. Food the percentage volume of each item was visually estimated. Data were then summarized and total percentage volumes ([sum of individual volumes of food]/[total volume of all samples] 100) were calculated to determine the foods of each species. Information on the most prevalent foods of each species was summarized to assess whether all species were eating the same foods. I used analysis of variance (ANOVA) on arcsine transformed percentages to assess differences between major foods. Student Newman Keuls multiple range tests were used for mean separation of foods between species and between dates. P 0.05) are mentioned in the text. In some cases, I present results separately by sex, age group, or month. In cases with small sample sizes, I used the nonparametric Mann Whitney test to ces. A similarity index was calculated using the percentage volumes to show relative similarity of the diets, SI ¼ 2W(A þ B), where W ¼ the sum of the similarities between each of the pairs of foods, and A þ B ¼ 200 (100% volume in 1st species and 100% vol ume in 2nd). Because M. septentrionalis often gleans, and the other species under consideration in this study are presumed to be aerial feeders, it would be logical to hypothesize that the food of M. septentrionalis might be quite different from that of the aerial feeders. To test this hypothesis, I compared the food of M. septentrionalis with that of the other species, particularly of M. lucifugus and M. sodalis , because they are the most similar in structure and have the most similar foods of the bats u nder consideration here. R ESULTS Relative percentages of major foods of the 7 main bats at (Appendix I). Only 2 silver haired bats were included in the sample, so the species could not be treated statisti cally. E. fuscus and N. humeralis fed most heavily on coleopterans followed by homopterans in N. humeralis . L. borealis fed most heavily on lepidopterans, followed by homopterans and coleopterans. fed on homopterans, coleopterans, and dipterans (35.7%, 22.6%, and 21.7%, respectively). With 1 exception, the main 3 foods by percentage volume were the same for M. sodalis, M. lucifugus , and M. septentrionalis : dipterans 1st, followed by lepidopterans, then coleopterans in M. lucifugus and by coleopt erans then lepidopterans for the other 2 species. The exception was that the M. lucifugus fed heavily on trichopterans (15.2%), the only species to feed appreciably on that food, whereas coleopterans were only 15.1% of the diet. Foods of bats of the genu s Myotis . The most heavily eaten foods of 107 individuals of M. septentrionalis (Table 1) from Prairie Creek were dipterans (37.5%), coleopterans (24.5%), and lepidopterans (20.7%). Among the beetles eaten by this species at Prairie Creek, scarabaeid beet les were most abundant. Spiders formed an appreciable portion of the diet overall (2.0%). The spiders are probably taken by gleaning. Juvenile M. septentrionalis had eaten 21.3% spiders, much of this item in July. On a seasonal basis, M. septentrionalis fe d heavily on dipterans in April, May, July, and September. Coleopterans formed a relatively high percentage in May August (17.7 74.7%), and a low percentage (8.8 11.5%) in April and September. Among coleopterans, scarabaeids were most heavily eaten in Jun e (41.3%), and Diabrotica in August (14.0%). Lepidopterans formed a relatively high percentage in April (19.4%), then decreased through May and June but increased again through the rest of the year. Cicadellids were most heavily eaten in late summer, parti cularly in August. Brown lacewings (Hemerobiidae) formed a small but stable amount of the food throughout the season. Mosquitos and scarabaeids formed 4.4% and 13.4% of the diet of female M. septentrionalis , and in both cases

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 108 this was greater than the am ount eaten by males (0.7% and 2.4% volume, respectively); total dipterans were higher in females than in males (41.4% and 24.0%, respectively), whereas lepidopterans and cicadellids were more heavily eaten by males than females (28.9% and 11.0%, as compare d with 19.5% and 1.6%). The cicadellids. Only 4 juvenile M. septentrionalis are included, but they appeared to feed more (greater volume percentages) on coleopterans, cicadellids, and spiders and less on lepidopterans than did the adults. The main foods of M. lucifugus were dipterans, lepidopter ans, trichopterans, and coleopterans (Table 1). This was the only species that fed appreciably on trichopterans at Prairie Creek. None of the differences by seas on, sex, or age within this species were M. sodalis were dipterans, coleopterans, and lepidopterans (Table 1). All monthly samples were small, but collectively the 3 foods represented a major proportion of food of M. sodalis throughout the season. D ipterans were more heavily eaten by males, lepidopterans by females (Appendix I). Foods of other species of bats . The major foods of 154 individuals of N. humeralis (Table 1) were beetles (60.1%), homopterans (20.4%, mostly cicadellids), and hemipterans (5.7%). Coleopterans formed roughly this percentage of the food throughout the season, varying from 46.9% to 73.7% during the various months, whereas homopterans (cicadellids) were eaten by N. humeralis primarily in July, August, and September, presumably months. Lepidopterans made up only 3.2% of the food overall. The most important coleopteran was the spotted cucumber beetle, Diabrotica undecimpunctata . Coleopterans were the most dominant food for N. humeralis , and m iscellaneous or coleopterans were heavily eaten (over 10% of the volume) in every month, but were most eaten in June and July. Scarabaeids were heavily eaten in May but not later. Diabrotica undecimpunctata was heavily eaten in late summer. Tri choptera and Lepidoptera were major items in May only. sexes of N. humeralis because only 4 males were included. Foods were similar between adults and juveniles (Appendix I). However, there were no carabids in the scats of juveniles, whereas this item comprised 9.9% of the volume of food in adult females. juveniles compared with 23.7%, u ¼ 811, P ¼ 0.18) . The carabids may have been fairly hard for the younger bats, and perhaps the due to inclusion of smaller beetles. Eptesicus fuscus fed heavily on coleopterans. They were the main food of this species in every month but April, ranging from 83% to 98% beetles by volume from May to October. The sample for April from Prairie Creek consisted of only 2 bats, which ate 25% Lepidoptera, plus Hemiptera (15%) and Ichneumonidae (32.5%; Table 1; Appendix I). Beetles were e aten equally by both sexes, 84.4% in females, 83.8% in males, followed distantly by pentatomids (7.6%, 6.3%). Volumes of food eaten by males and females were quite similar in most greater amounts by females ( u ¼ 704.5, P ¼ 0.004). Seasonally, scarabaeids were most heavily eaten in May, June, and July, with the values from May and June all other months . Carabids were eaten in October, August, July, and May. cantly greater volume of the diet in April (probably when prey was limited). Lasiurus borealis favored moths (Table 1). Only a small number of red ba ts was taken in April July or in October (1, 3, 1, 3, and 4 bats); lepidopterans formed

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 109 85%, 50%, 0%, 35%, and 85% of the volume in those months. In August and September, larger numbers of red bats were included (17 and 14) and moths formed 49% and 93% of the diet by volume. Lepidopterans thus formed a major part of the food of L. borealis throughout the year. Coleoptera had the 2nd greatest volume overall (10.7%), which varied during the months from 0% to 67%. Homopterans (mostly cicadellids), coleopter ans, dipterans, and lepidopterans were the most abundant foods in feces of 27 examined from Prairie Creek (Table 1). Cercopids were found in feces of males only, and dipterans were more abundant in females. Dipterans were highest in May, June, and September. Cicadellids were taken in ever increasing numbers from May through August. Coleopterans were present in the diet of and were relatively high in June August; ants (Formicidae) occurred only in July (17.0%), trichopterans were high est in May (9.0%) and September (10.0%), and lygaeids were highest in June differences in diet by month for involved dipterans, cercopids, and lygaeids. Fecal pellets from only 2 individuals of L. noctivagans were available. These were taken on the same date (3 October 1994), and each contained 5 foods with percentage volumes as follows: Lepidoptera (43.5%), brown lacewing, Hemerobiidae (30%), ant, Formicidae (7.5%), Diptera (2.3%), and midge, Chironomidae (1.5%). Foods of bats eaten on a single night . Foods of 34 bats of 6 species taken on 1 date at 1 site (16 August 1998) at Prairie Creek were compared as a further test of whether foods were taken based on availability. The foods eaten by these bats (Table 2) s howed similar variation to the larger sample. In both samples, beetles were the main foods of both N. humeralis and E. fuscus and higher in E. fuscus . Moths were low in both. Cicadellids were important in both of these species but were much more important in N. humeralis . Moths were the main food of L. borealis , followed by cicadellids. fed on cicadellids, beetles and moths; M. septentrionalis and cicadellids; and M. lucifugus fed on cicadellids, Thus, on a single night with bats all captured at the same place, the various sp ecies fed on different prey but the diet was similar to that expected based on observations over longer periods (Table 1). Food as related to size of bat . The food habits of 7 species of bats from Prairie Creek were examined by decreasing size of bat (T able 3). There was no apparent relationship between size of bat and food. The largest bat was a beetle feeder (about 80% beetles), the 2nd largest was a moth feeder (64.4% moths), the 3rd largest was again a beetle (60%) and leafhopper (20%) feeder. The th ree species of Myotis were the most similar, even though one, M. septentrionalis , has the ability to glean. The species of Myotis fed heavily on dipterans, lepidopterans and coleopterans, although M. lucifugus took quite a few trichop terans. The smallest b at, the pipistrelle, fed on cicadellids, beetles, dipterans, and lepidopterans. No correlations existed between size of bat and proportion in the diet for Coleoptera ( r ¼ 0.643, P ¼ 0.589), Lepidoptera ( r ¼ 0.107, P ¼ 0.819), Cicadellidae ( r ¼ 0.429, P ¼ 0 .337), and Diptera ( r ¼ 0.643, P ¼ 0.119). Similarity of diets among species . Similarity of foods eaten by the various species is indicated by similarity indices (SI). The 3 species of Myotis have the highest similarity in food habits (Fig. 1). vus ts loosely into this grouping, whereas it is much less consistent with the E. fuscus N. humeralis group at

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 110 0.429. shows a SI index with N. humeralis of 553. This is because both fed highly on Coleoptera and Hemiptera . L. borealis loosely into this group, with a SI of 0.402. Likewise, L. borealis is distant but closer to the Myotis stem than to the E. fuscus N. humeralis stem. D ISCUSSION The bats under study were selecting different foods from among the available items. Why? Thi s is a complicated question, but has been partially discussed by Brigham (1990), Fenton (1987), Kunz (1988), and Whitaker (1994). By necessity, foods eaten by bats are most similar to available foods when foods are limited because the bats have little choi ce at that time. This is most likely to occur early and late in the season (Whitaker 1995) or perhaps in the high latitudes (see Barclay 1985). When conditions are good, such as in midseason, bats usually select from a variety of various hyme nopterans, and often others. ants, are irregularly available but are apparently highly desired (see Brigham 1990). Reasons for selectivity probably ultimately relate to an initial evolutionary division of food supplies by bats through competitive and Vaughan (1980) and as discussed by Wiens (1977). It is presumably advantageous for different species of bats t o feed on different foods to minimize competition. Once they begin to feed on differing foods, they can undergo evolutionary adaptation to better feed on their differing prey. Bat species differ in size, speed, behavior, echolocation, and strength of jaws, and insects vary greatly in size, speed, and behavior. All of these factors, different habitats and in different ways and to feed on differing foods. a not All the species had access to the entire Prairie Creek area and all of its food resources. However, because of their varying habits and preferred foraging habitats, and echolocat ion characteristics, the various species of bats forage in different areas, presumably to take advantage of selected foods where they occur. However, it is not advantageous for bats to become overspecialized to feed on only 1 or a few kinds of insects. Rat her, even though they have some feeding adaptations, they have retained the ability to feed on a large number of items, which serves to allow them to take more of whatever is available when food is limited. Eptesicus fuscus and N. humeralis have heavy ja ws (Freeman 1981), allowing them to feed on larger beetles and hemipterans. L. borealis has long narrow wings (Aldridge and Rautenbach 1987; Fenton 1983), allowing capture moths, many of which have various protective mechanisms. Myotis a nd have broad wings and more slowly in crowded habitats. Bats also differ greatly in size. In Indiana, for example, bats range from , with an 18 cm wingspread and a small b ody and mouth, to L. cinereus , with a wingspread up to about 38 cm and with a large mouth. This allows for major differences in the size of foods that can be eaten. Insects eaten by bats must be small enough to enough to be e Adaptation by size classes of insects is not entirely apparent from my data. For example, the coleopterans eaten by E. fuscus (which has a body mass of 16.0 g) average much larger than those eaten by M. lucifugus (mass of 6.2 g). Many of t hese differences are masked by grouping insect prey remains under ordinal categories such as Coleoptera, Lepidoptera, or Diptera. Differences in sizes of food items among species of bats would probably be much more pronounced if we could identify all foods of bats to family or species and to quantify variation in size of prey. See Whitaker and Clem (1992), Whitaker (1994), and Brigham and Saunders (1990) for more information on N. humeralis and E. fuscus . Figure 1 . Dendrogram showing dietary relatioships of bats at Prairie creek, Vigo County, Indiana. The highest numbers indicate the greatest similarity in food habits.

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 111 Trichopterans deserve special comment. They, alon g with ying ants and termites, are apparently highly desirable to many species of bats, as they are eaten by many species of bats when available, although they are intermittent in occurrence. That M. lucifugus , but no other species at Prairie Creek, fed h eavily on these was unexpected. It would appear that trichopterans were not widespread at Prairie Creek, but that they were abundant where M. lucifugus was feeding for a short period in midsummer. Apparently other species were not aware of the trichopteran s. The various species of bats at Prairie Creek differed in the major foods eaten. A number of mosquitos (Culicidae) were eaten by bats examined during this study, although most bats, contrary to popular opinion, do not eat many mosquitos (Whitaker and L ong 1998). The study area is in a swamp where mosquitos were numerous. Whitaker and Long (1998) have proposed that most of the mosquitos eaten by bats may be from male swarms. This may be the situation at Prairie Creek, or it may be that so many mosquitos were present that it was inevitable that some were taken by the bats. Studies of wing morphology by Aldridge (1986), Aldridge and Rautenbach (1987), and Norberg and Rayner (1987) and of echolocation by Neuweiler (1984) and Neuweiler and Fenton (1988) hav e led to hypotheses about foraging habitats and strategies of various species of bats. Bats with broad wings can y slowly and hover, and bats with high frequency and short duration calls (whispering bats) can pick up detail at short range. These calls hav e the added advantage of not being audible at a very great range, thus helping keep prey from echolocation characteristics items from surfaces, i.e., to glean. Analysis of food habits can provide clue s that a species might be a gleaner, through the presence of non ying items, such as spiders, crickets, or caterpillars. Myotis septentrionalis has the wing structure and echoloca tion calls characteristic of gleaners, and Miller and Treat (1993) recorde d this species picking insects off a backlit screen. Faure et al. (1993) also demonstrated this species to be a gleaner. This species often feeds on spiders. In a sample of 172 fecal pellets from Arkansas examined by Whitaker, spiders occurred in 8 (4.7%) fecal pellets and made up an estimated 1.3% of the volume (J. D. Wilhide, in litt.). Brack and Whitaker (2001) found spiders in 16 of 63 (25.4%) fecal pellets M. septentrionalis taken by harp trap at Copperhead Cave, a mine in Vermillion County, Indiana, f orming 9.1% of the total volume of food in that sample. Comparison of the food of M. septentrionalis was not radically different from that of M. sodalis or M. lucifugus (Table 47). The similarity of these data might suggest that these 3 species are feedi ng in much the same manner, whether it be gleaning or hawking or both. Spiders were the only clearly non ying items taken regularly during this study and provide the strongest evidence for gleaning, but they were taken only by M. septentrionalis . Because the remainder of the food was so similar, I suspect that M. septentrionalis and the other 2 species were getting most of their food by hawking, but that M. septentrionalis is

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 112 supplementing this by gleaning (mostly spiders). I consider this hypothesis as tenable, but I think that there would probably be more differences in foods if this were the case. Possib ly all 3 species of Myotis were spending some time gleaning. If so, it would appear that all 3 should take numerous spiders. That this hypothesis could be tenable is supported by data on M. lucifugus from Alaska. M. lucifugus is not considered to be a glea ner and usually does not eat many spiders. However, Whitaker and Lawhead (1992) examined 100 fecal pellets from M. lucifugus from Alaska. These bats were using 3 foods, lepidopterans (71.1% volume), spiders (16.8%), and dipterans (3.7%). The spiders were f ound in 36 of the pellets. Because of the 24 h daylight, bats in Alaska must feed in daylight in June. I suggest that the large percentage of spiders eaten by this species in Alaska indicates that these bats were spending much of their foraging time in the forest gleaning rather than hawking insects in daylight in the open air, where exposure to diurnal predatory birds could be substantial. If the Alaskan bats were getting spiders by gleaning and thus avoiding predators, it might follow that much of their o ther food (i.e., many or most of the lepidopterans and dipterans) were also captured by gleaning. If that were true, I suggest that many of the lepidopterans and dipterans eaten by M. septentrionalis at Prairie Creek could have been gotten by gleaning, and further, if M. lucifugus gleans in Alaska, then it and M. sodalis might also glean at Prairie Creek. The occurrence of spiders as food items indicates that M. septentrionalis is gleaning to some degree, but there was no solid evidence that the other 2 s pecies of myotis were gleaning at all. This suggests that M. septentrionalis gleaned more than the other 2 species, but that none of the 3 species was spending appreciable time gleaning. This appears to me to be the most tenable hypothesis for the bats at Prairie Creek. Perhaps many species of bats, such as M. lucifugus , can glean at times, and some, such as M. septentrionalis , glean more often and become adapted for it. Faure et al. (1993) found that the calls of the gleaning insectivorous bat M. septent rionalis are less detectable to noctuid moths than are those of aerial feeding M. lucifugus . It is possible that M. lucifugus (and M. sodalis ) glean more than previously suspected even though they are not as M. septentrionalis . If so, it would seem likely that these species may use different styles of echolocation when gleaning than when aerial hawking. See Anthony and Kunz (1977), Brack and Laval (1985), and Bra ck and Whitaker (2001) for additional information on food of these bats. A CKNOWLEDGMENTS My thanks go to M. B. Fenton and T. H. Kunz for their many valuable suggestions on this article. Thanks also to F. Lindley and L. Castor for the statistical analysi s and to L. Bakken for typing. The protocol was approved by Indiana State Animal Care and Use Committee and followed ASM guidelines. L ITERATURE C ITED A LDRIDGE , H. D. J. N. 1986. Manoeuvrability and ecological segregation in the little brown ( Myotis luci fugus ) and Yuma ( M. yumanensis ) bats (Chiroptera: Vespertilionidae). Canadian Journal of Zoology 64:1878 1882. A LDRIDGE , H. D. J. N., AND I. L. R AUTENBACH . 1987. Morphology, echolocation and resource partitioning in insectivorous bats. Journal of Animal E cology 56:763 778. A NTHONY , E. L. P., AND T. H. K UNZ . 1977. Feeding strategies of the little brown bat, Myotis lucifugus , in southern New Hampshire. Ecology 58:775 786. B ARCLAY , R. M. R. 1985. Long versus short range foraging strategies of hoary ( Lasiur us cinereus ) and silver haired ( Lasionycteris noctivagans ) bats and the consequences for prey selection. Canadian Journal of Zoology 63:2507 2515. B ELWOOD , J. J., AND M. B. F ENTON . 1976. Variation in the diet of Myotis lucifugus (Chiroptera: Vespertilioni dae). Canadian Journal of Zoology 54:1674 1678. B RACK , V., J R ., AND R. K. L AVAL , J R . 1985. Food habits of the Indiana bat in Missouri. Journal of Mammalogy 66:308 315. B RACK , V., J R ., AND J. O. W HITAKER , J R . 2001. Foods of the northern myotis, Myotis sep tentrionalis , from Missouri and Indiana, with notes on foraging. Acta Chiropterologica 3:203 210. B RIGHAM , M. 1990. Prey selection by big brown bats ( Eptesicus fuscus ) and common nighthawks ( Chordeiles minor ). American Midland Naturalist 124:73 80. B RIGH AM , M., AND M. B. S AUNDERS . 1990. The diet of big brown bats ( Eptesicus fuscus ) in relation to insect availability in southern Alberta, Canada. Northwest Science 64:7 10. F AURE , P. A., J. H. F ULLARD , AND J. W. D AWSON . 1993. The gleaning attacks of the nor thern long eared bat, Myotis septentrionalis , are relatively inaudible to moths. Journal of Experimental Biology 178:173 189. F ENTON , M. B. 1983. Just bats. University of Toronto Press, Toronto, Ontario, Canada. F ENTON , M. B. 1987. Echolocation, insect h earing, and feeding ecology of insectivorous bats. Pp. 261 285 in

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 113 Ecology of bats (T. H. Kunz, ed.). Plenum Press, New York. F ENTON , M. B., AND G. K. M ORRIS . 1976. Opportunistic feeding by desert bats ( Myotis spp.). Canadian Journal of Zoology 54:526 530. F REEMAN , P. W. 1981. Correspondence of food habits and morphology in insectivorous bats. Journal of Mammalogy 62:166 173. K UNZ , T. H. 1988. Methods of assessing prey availability for insectivorous bats. Pp. 191 210 in Ecological and behavioral methods f or the study of bats (T. H. Kunz, ed.). Smithsonian Institution Press, Washington, D.C. M ILLER , L. A., AND A. E. T REAT . 1993. Field recordings of echo location and social sounds from the gleaning bat, Myotis lucifugus . Bioacoustics 5:67 87. N EUWEILER , G . 1984. Foraging, echolocation and audition in bats. Naturwissenschaften 71:446 455. N EUWEILER , G., AND M. B. F ENTON . 1988. Behaviour and foraging ecology of echolocation bats. Pp. 535 549 in Animal sonar: processes and performances (P. Nachtigall, ed.). Plenum Press, New York. N ORBERG , U. M., AND J. M. V. R AYNER . 1987. Ecological morphology foraging strategy and echolocation. Transactions of the Philosophical Society of London (Biology) 316:355 427. HEA , T. J., AND T. A. V AUGHAN . 1980. Ecological observations o n an East African bat community. Mammalia 44:485 496. W HITAKER , J. O., J R . 1994. Food availability and opportunistic versus selective feeding in insectivorous bats. Bat Research News 35:75 77. W HITAKER , J. O., J R . 1995. Food of the big brown bat, Eptesic us fuscus , from maternity colonies in Indiana and Illinois. American Midland Naturalist 134:346 360. W HITAKER , J. O., J R . 1996. Bats of Prairie Creek, Vigo County, Indiana. Proceedings of the Indiana Academy of Science 105:87 94. W HITAKER , J. O., J R ., AN D P. C LEM . 1992. Food of the evening bat, Nycticeius humeralis , from Indiana. American Midland Naturalist 127:211 214. W HITAKER , J. O., J R ., AND B. L AWHEAD . 1992. Foods of Myotis lucifugus in a maternity colony in central Alaska. Journal of Mammalogy 73:6 46 648. W HITAKER , J. O., J R ., AND R. L ONG . 1998. Mosquito feeding by bats. Bat Research News 39:59 61. W IENS , J. A. 1977. On competition and variable environments. American Scientist 65:590 597. Submitted 13 November 2002. Accepted 26 May 2003. Associat

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 118 Bats and Integrated Pest Management Seventy percent of all bats eat insects, including many crop and forest pests. A cooperative publication of the USDA Natural Resources Conservation Service, t he Wildlife Habitat Management Institute, and Bat Conservation International, Inc. Amazing Bat Facts Over 1,000 kinds of bats account for about a quarter of all mammal species, and most are highly beneficial. Bats are the only mammals capable of self pr opelled flight, and they live on every continent except Antarctica. Contrary to popular misconceptions, bats are not blind, do not become entangled in human hair and seldom transmit disease to other animals or humans. Not only do bats see as well as othe r mammals, they also use echolocation to detect objects as fine as a human hair in total darkness, Though bats are long lived (some living up to 34 years), they reproduce slowly, Most species bear and nurse just one pup per year. The pallid bat ( Antrozou s pallidus ) of western North America is immune to the stings of scorpions and even the seven inch (125 cm.) centipedes upon which it feeds. eared bats ( Corynorhinus townsendii ) can maneuver like helicopters to pluck insects from foliage or to drink from tiny pools. In contrast, Mexican free tailed bats ( Tadarida brasiliensis ) are built like jets, require large open spaces to maneuver and fly up to 10,000 feet (3,000m) high. Like most animals, bats suffer from habitat loss and environmental pollution, but the primary cause of their decline is wanton destruction by humans. Loss of bats can increase the demand of chemical pesticides, jeopardize whole ecosystems, and harm human economies. Agricultural Allies Bats are primary predators of beetl es, moths, leaf hoppers, and other insects that cost farmers and foresters billions of dollars every year. They also devour mosquitoes in our backyards. Without predators, insects would soon overwhelm the earth. Like birds, bats consume enormous quantitie s. Mexican free tailed bats ( Tadarida brasiliensis ) from just three caves near San Antonio, Texas, eat approximately a million pounds nightly, including many crop pests. Illustrative of the impact that even small colonies of bats can have, just 150 big br own bats ( Eptesicus fuscus ) can eat sufficient cucumber beetles each summer to protect larvae, pests that cost American farmers and estimated billion dollars annually. One Georgia pecan grower was losing 30% of his pecan crop to hickory shuckworms and other major southeastern pests. For the past two years, after installing bat houses, he has seen no further crop damage. One bat house now hosts a colony of more than 2,000 bats. One little brown myotis ( My otis lucifugus ) can catch 1,200 mosquito sized insects in just one hour, sometimes catching two in a single second. A nursing mother eats more than her own body weight nightly, meaning that colonies can consume vast numbers nightly. Many garden pests can hear bats from over 100 feet (30m) away and will avoid areas where bats are present. Researchers have shown that, by playing even fake bat sounds over test plots of corn, they can scare corn earworm moths away, reducing damage from their larva by 50%. A r ed bat ( Lasiurus borealis ) that eats even 100 moths may prevent egg laying that could otherwise produce Silver haired bats ( Lasionycteris noctivagans ), western long eared myotis ( Myotis evotis ) and many other bat species help keep countless forest insects in check. Pallid bats ( Antrozous pallidus ) benefit ranchers by consuming large quantities of grasshoppers and crickets. The hoary bat ( Lasiurus cinereus ), the only land mammal native to Hawaii, o ften feeds on sugarcane leafhoppers, a

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 119 Incorporating Bats into Integrated Pest Management The most important threat to bats is loss of natural roosts. You can help, and reduce insect pests, by providing alternative homes for bats that feed on your property by: building a bat house, and placing it at least 10 12 feet (3 4m) off the ground on a pole or the side of a building, working with highway departme nts to create roosts in nearby bridges, and decreasing disturbance to nearby bat roosts in caves and mines by educating the local community about the importance of bats, providing signs at the entrances of caves or mines where bats live or erecting bat fri endly gates at entrances to minimize human disturbance. and the Building Homes for Bats video provide easy to follow instructions for attracting bats. The Bats and Mines resource publication provides detailed plans for pr otecting bats in caves and mines. The Bats in American Bridges handbook provides instructions on how to benefit from attracting thousands of bats to bridges. The Forest Managemnt & Bats publication provides basic forest management practices that improve fo rest health and productivity which also maintain and enhance habitat for bats. The Water for Wildlife handbook for landowners and range managers describes proven methods for increasing wildlife safety ad accessibility at artificial watering features withou t diminishing their usefulness for livestock. All are available from Bat Conservation International. Enhancing Natural Habitat Bats need more than just a nice place to roost during the day. They must feed and drink every night. Having a variety of good habitat types in close proximity will make your property more attractive to bats. Promote good habitat by: Providing clean, open water in ponds or lakes. Maintaining hedge rows and wind breaks. Preserving areas along forest edges as well as old trees. Com mon Insect eating Bats Eastern red bat, Lasiurus borealis little brown myotis, Myotis lucifugus Mexican free tailed bat, Tadarida brasiliensis pallid bat, Antrozous pallidus big brown bat, Eptesicus fuscus silver haired bat, Lasionycteris noctivagans Livi ng Safely With Bats Like most other mammals, bats can contract rabies. However, the risk of exposure from bats is extremely remote for anyone who simply keeps them outside and leaves them alone. To protect your family, vaccinate dogs and cats and caution c hildren never to handle any unfamiliar animal. Contact Information USDA Natural Resources Conservation Service (NRCS) Contact your local NRCS Field Office (A directory of all states and their offices can be found at Wildlife Habitat Ma nagement Institute 100 Webster Circle, Suite 3 Madison, MS 39110 (607) 607 3131 For more information about attracting and living safely with bats, or to obtain resource publications, contact: Bat Conservation International P.O. B ox 162603 Austin, Texas 78716 (512) 327 9721

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 120 Economic Value of the Pest Control Service P ro vided by Brazilian free tailed Bats in S outh central Texas Cutler J Cleveland 1 * , Margrit Betke 2 , Paula Federico 3 , Jeff D Frank 4 , Tho mas G Hallam 3 , Jason Horn 5 , Juan D López Jr 6 , Gary F McCracken 3 , Rodrigo A Medellín 7 , Arnulfo Moreno Valdez 8 , Chris G Sansone 9 , John K Westbrook 6 , and Thomas H Kunz 5 1 Center for Energy and Environmental Studies and Department of Geography and Environment, Boston University, 675 Commonwealth Avenue, Boston, MA 02215 *(; 2 Department of Computer Science, Boston University, Boston, MA 02215; 3 Department of Ecology and Evolutionary Biology, 569 Dabney Hall, University of Tennessee, Knoxville, TN 3 7996; 4 Indigo Systems, 70 Castilian Dr, Goleta, CA 93117 3027; 5 Center for Ecology and Conservation Biology, Department of Biology, Boston University, Cummington Street, Boston, MA 02215; 6 Areawide Pest Management Research Unit, USDA ARS, 2771 F and B Road , College Station, TX 77845; 7 Instituto de Ecología, UNAM, Ap Postal 70 275, 04510 Ciudad Universitaria, DF, Mexico; 8 Instituto Tecnológico de Cd Victoria, Bulevard Emilio Portes Gil # 1301, Cd Victoria, Tamaulipas, CP 87010, México; 9 Texas A&M University Research and Extension Center, 7887 US Highway 87 North, San Angelo, TX 76901 ABSTRACT Brazilian free tailed bats ( Tadarida brasiliensis ) form enormous summer breeding colonies, mostly in caves and under bridges, in south central Texas and northern Mexico . Their prey includes several species of adult insects whose larvae are known to be important agricultural pests, including the corn earworm or cotton bollworm ( Helicoverpa zea ). We county region in south central Texas. Our calculations show an annual value of $741 000 per year, with a range of $121 000 $1 725 000, compared to a $4.6 $6.4 million per year annual cotton harvest. Front Ecol Environ 2006; 4(5): 238 243 Th roughout the world, humans compete with a multitude of pest species for food, fiber, and timber, although natural predators greatly reduce the densities of many of these pests. Loss of natural pest control services could have important economic, environmental, and huma n health consequences (Daily 1997). The Brazilian free tailed bat ( Tadarida brasiliensis ; Figure 1) provides a continental scale, natural pest control service in North America. This species overwinters in south and central Mexico and migrates north each sp ring to form large breeding colonies in northern Mexico and the southwestern United States (Davis et al . 1962). Historic records of some summer cave colonies of this species reportedly exceed 20 million individuals. Over 100 million bats may disperse night ly from caves and bridges in south central Texas to feed. These bats consume enormous quantities of insects throughout the warm months; lactating females, in particular, may ingest up to twothirds of their body mass each night (Kunz et al . 1995). The prey of these bats includes adults of several Lepidopteran species in the family Noctuidae (Lee and McCracken 2002, 2005), whose larvae are known agricultural pests, such as fall armyworm ( Spodoptera frugiperda ), cabbage looper ( Trichoplusia ni ), tobacco budwo rm ( Heliothis virescens ), and corn earworm or cotton bollworm ( Helicoverpa zea). The cotton bollworm is among the most destructive agricultural pests in the Americas. Here we evaluate the magnitude of this previously unaccounted pest control service in cot ton. The study area The study area covered an eight county region (Uvalde, Medina, Zavala, Frio, Dimmitt, LaSalle, McMullen, and Atascosa Counties) in southwest Texas, including the four county Winter Garden region located southwest of San Antonio (Figure 2). This area has agricultural production capable of supporting insect prey upon which T brasiliensis feeds. In recent years, about 10 000 acres of cotton have been harvested in this region, with a market value of between $4.6 and $6.4 million. The region is characterized by a high input, high yield system, with extensive use of irrigation water, fertilizer, pesticides, and other inputs. Cotton is planted in February or March and harvested in August and September, with typical yields of 680 kg (600 lb) to 1250 kg (1100 lb) of lint per ha. The price of cotton ranges from $0.50 to $0.70 per pound and the price of seed from $80 to $120 per ton.

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 121 There are several colonies of Brazilian free tailed bats in the San Antonio Uvalde region (Figure 2), and evidence strongly suggests that individual bats from these colonies feed in and above the agricultural fields in the Winter Garden region at the time of major emergences of insect pests from those fields. First, agricultural production in the area supports large p opulations of insect pests, most notably the corn earworm or cotton bollworm, initially in wildflowers and corn, which serve as a nursery crop (Kennedy and Margolies 1985). Second, high levels of foraging activity and consumption of insects by bats have be en documented in the midst of large moth populations at altitudes of 200 1200 m (Wolf et al . 1994). Third, dietary and DNA analysis of bat feces indicate that H zea and other agricultural pests constitute a significant fraction of the diet of T brasiliensi s (Kunz et al . 1995; Whitaker et al . 1996; Lee and McCracken 2002, 2005; McCracken et al . 2005). Fourth, our NEXRAD Doppler radar data (Figure 2) clearly show that the nightly dispersal of bats from their cave and bridge roosts, spreading out over the Wint er Garden region, is closely associated in time and space with major emergences of bollworm moths (Beerwinkle et al . 1994). Finally, our ground based visual observations of nocturnal activity over these cotton fields reveal a great deal of foraging behavio r by T brasiliensis at the time that bollworm moths are emerging. While there is strong evidence that Brazilian freetailed bats feed on H zea , we are less certain about the number of bats that forage over the Winter Garden cotton crop. T . brasiliensis has an average flight speed of 40 km hr 1 and a nightly flight range of over 100 km (Williams et al . 1973), placing a number of large colonies of this species well within reach of the Winter Garden crops. At least three cave colonies, one sinkhole colony, and five bridge colonies are adjacent to cropland that supports corn and cotton production (Figure 2). Using a combination of historic estimates (McCracken 2004) and recent census data from these sites (M Betke et al . unpublished), we make a conservative esti mate that at least 1.5 million bats feed nightly over the agricultural fields in the Winter Garden region. Valuing pest control services We use an avoided cost approach that places a value on pest control by assessing the costs or expenditures that socie ty avoids as a result of the availability of these services as an input to production. This cost has two components: the value of the cotton crop that would have been lost in the absence of the bats and the reduced cost of pesticide use private and socia l attributable to the presence of bats. These methods have been applied to services provided by wetland ecosystems (Woodward and Wui 2001), but so far have not been used to assess pest control services. The unit for our analysis is the individual female bat, because relatively few males roost in these large maternity colonies. Because damage to the crop occurs in the larval stage of H zea , our goal was to estimate the number the presence of a single bat. Th e overall impact on agriculture is estimated by scaling up our population estimates of bat colonies in the study area. The model we develop is a generalized case, based on the most recent and authoritative data available. Two principal sources of variabili ty are the key parameters in our model. The first is our uncertainty about some aspects of the behavior of the bats and their insect prey. This can be bounded and our results can be tested by their sensitivity to our assumptions of this uncertainty. The se cond and more interesting source of variation stems from the relation between pest control services supplied Figure 1 . The Brazilian free tailed bat ( Tadarida brasiliensis )

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 122 by the bats at the adult stage of the pest and (1) pest control supplied by other natural enemies and environmental stresses at earlier stages in t he life cycle of H zea , and (2) control supplied by farmers through the application of pesticides. We elaborate on this point below. Although the temporal scale of our study was restricted to a single growing season, the uncertainties of bat population dyn amics do not affect this scale. A single female Brazilian free tailed bat (at peak lactation) weighing 12.5 g will consume about 8.1 g of adult insects each night (Kunz et al . 1995). Fecal analysis indicates insects of the order Lepidoptera (Lee and McCracken 2002, 2005). The fraction of eaten Lepidoptera that are bollworms is less certain. Because dietary analysis shows that moth consumption increases two to three fold during peak bollworm availability (Lee and McCracken 2005), we assume that this increased moth consumption consists largely of bollworms. This translates to 30 60% of the 20 adult bollworms eaten by a single bat each night. The mass of a moth abdomen, the part consumed by bat s, is about 0.07 g. We also assume that approximately half of the moths consumed by a bat are female and not all would have infested crops in the Winter Garden area; some may move to other hosts, while others will migrate out of the region. We further assu me that 10 20% of the moths eaten by a bat would have dispersed into a crop in the region. Thus, in the middle of this range, a single bat will eat about 1.5 female moths each night that would otherwise have laid eggs on a single host plant within the stud y area. The next set of calculations is based on the population dynamics and life history of H zea (Sansone et al . 2002). A single female will lay 600 1000 eggs in her lifetime. Natural enemies such as ants, beetles, and parasites reduce survivorship to 2 5% through all stages of development (Sansone and Smith 2001), yielding 2% of 600 to 5% of 1000 adult moths. Using the mean value in each range of these survival estimates, a single bat consuming 1.5 adult moths per night will, in effect, prevent about f ive larvae from damaging crop plants nightly. The next step is to translate the larvae bat to the economic value of the damage that these larvae would have inflicted. A single larva will destroy two to three b olls of cotton in its lifeti me. However, we correct for the fact that the susceptibility of the cotton plant declines over the course of the growing season, because the contribution of fruit set earlier in the season is more valuable than fruit set later in the season (Sansone et al . 2002). That is, fruiting branches set later in the season contribute far less to actual lint yield compared to branches set early in the season. The first third of the fruiting branches set generate about half of the ultimate lint production; the final th ird accounts for just 7% (Sansone et al . 2002). As a result, a single bat consuming 1.5 adult moths per night could prevent damage to upwards of 10 bolls per night in mid June, but close to zero by the end of the growing season in early August. With the p rice of cotton in 2001 at about $.0017 per boll, this means a single Brazilian free tailed bat provides a service of $0.02 per night in mid June, declining to close to zero by August. Figure 2. The 8 county study area (red outline) lies to the southwest of San Antonio Texas and includes colonies of T brasiliensis located in caves (circles) and concrete highway bridges (crosses). Areas of agricultural production are shown in dark green. Also shown is NEXRAD Doppler RADAR imagery of bats returning from nightl y foraging over agricultural land. Each pixel corresponds to approximately 1 km 2 of reflectivity from bats aloft. Darker colors indicate greater reflectivity and hence greater density of bats. Large areas of reflectivity are seen twice nightly at the tim e of emergence and again when bats return to their roosts. The timing, directionality, and density of the reflectivity suggest that large numbers of bats forage over this area of agricultural production, consuming significant quantities of pest insects.

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 123 The role of pesticides t he use of pesticides; when does the potential injury from a pest justify the cost of a pesticide application? In the Winter Garden region, the economic threshold for H zea is breached at a density of 8000 10 000 larvae per acre, although treatments to cont rol H zea in cotton production in the study area vary substantially across farms and time. Such densities generally do not occur until early July, when corn is no longer a viable host for the larvae. Thus, the first week in July is typically when the pesti cides are initially applied, which might be followed by as many as three additional applications, spaced about 7 days apart, the last one occurring in the final week of July. A pesticide application eliminates close to 100% of H zea eggs and close to 90% o f its larvae; however, these effects are short lived. After just 2 3 days, egg survivorship increases from almost zero to 80%, several times higher than what it was prior to pesticide applications. Pesticides have both private and social costs. The priva te component is the cost to the farmers of purchasing and applying the chemicals. In the Winter Garden region, a typical single application of synthetic pyrethroid insecticide to control H zea costs about $25 ha 1 , with application rates of about 0.03 lb ( 0.014 kg) of active ingredient used per acre. Social and environmental costs include public health costs, the loss of natural enemies, the loss of pollination services, losses to fish and birds, and groundwater contamination, as well as others, which we es timate at $24.38 kg 1 (11.06 lb 1 ) of active ingredient of pesticide (Kovach 2003). This value is based on Pimentel et al environmental cost of pesticide use in the US at $8.1 billion s (1995) estimate of 332 million kg (732 million lb) of active ingredients of pesticide use in the US in 1992. Results Our results in the case where we assume no use of pesticides are presented in Figure 3a. The reference case places the key demographic v ariables for H zea (survivorship rates for eggs and larvae) at the mean values of their observed ranges. The high and low cases use values at their observed extremes. The annual value has two components. The first is the cumulative value of the avoided dam age provided by T brasiliensis from June 10, the approximate date when the transition of H zea from corn to cotton is complete, to August 8, the approximate date when cotton is no longer susceptible to damage from H zea . In the reference case, the cumulati ve annual value of this first component is $638 000 (Table 1). The second component of this service is the avoided cost of pesticides. In our reference case, from mid June to early July, a population the development of abo ut 5 million larvae per night. If we assume that these larvae would have been distributed evenly across the 4000 ha of cotton, then the economic threshold of 20 000 25 000 larvae ha 1 (8000 10 000 acre 1 ) would be reached in about 12 days; in the low egg/l arvae mortality case, these densities are reached in just a few days. Thus, it is quite plausible that the bats prevent one, and perhaps two, applications of pesticides in the early stages of the cotton crops. Of course, there would be other sources of mor tality for H zea in the absence of T brasiliensis , but the magnitude of consumption by these bats suggests that their loss would be considerable. At about $25 ha 1 per pesticide application, one avoided pesticide application across all 4000 ha would be wor th $100 000. In Table 1 we present the impact of zero, one,

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 124 and two avoided applications, generating a range of zero to $200 000 for the avoided cost of pesticide use. The associated social and environmental avoided costs range from zero to $6000. Our res ults in the case where we assume farmers do use pesticides to control H zea is presented in Figure 3b. Again, the reference case places the key demographic variables for H zea (survivorship rates for eggs and larvae) at the mean values of their observed ra nges. The high and low cases use values at their observed extremes. Figure 3b compares the reference case with no pesticides to one in which pesticide applications are made on July 7, 14, 21, and 28. The cumulative value in the case with pesticides is just 10% lower than the case with no pesticides. Discussion Our estimate of the value of the pest control service provided by Brazilian free tailed bats to agriculture ranges from 2 29% of the $6 million value of the cotton crop in the Winter Garden region; t he reference case value is about 12%. This suggests that the bats do indeed play a vital role in protecting this crop from damage, and in reducing the costs of pestic ide use to farmers and society. One of the distinctive features of this service is that it accrues largely in the early part of the growing season (Figure 3a). Eighty percent of the annual value of the pest control service in the study area accumulates before the end of the first week of July, which in practice is when farmers consider their fi rst application of pesticides. This result is consistent with the behavior of an effective natural enemy in ephemeral crop habitats, namely the extension of the latent phase of population growth by a vagile, polyphagic population that is well established i n the area before the pest moves into the target crop (Wiedenmann and Smith 1997). Because cotton fields are ephemeral, extension of the latent phase of population growth when pest densities are relatively low and slow growing reduces the time availabl e for the epidemic phase, where explosive growth can breach thresholds that cause plant damage and trigger chemical intervention. The magnitude of the consumption of moths strongly suggests that T brasiliensis reduces crop damage, eliminates at least one a pplication of pesticide, and possibly delays the time when pesticides are first used. Each of these impacts has positive economic and environmental benefits. There is a clear tradeoff among different forms of natural enemy control in this agroecosystem. In years when mortality rates are high for the egg and larval stages of H zea , the number of larvae prevented from reaching the moth stage by the bats is reduced. Conversely, in years when control by natural enemies at those early stages is relatively low, the impact of the bats is much greater. The use of pesticides to control H zea in this region does not significantly reduce the value of the pest control by T brasiliensis (Figure 3b). This is due to two factors. First, pest control by bats is concentra ted in the early part of the cotton growing season, when pest densities are not high enough to trigger a pesticide application. Second, the reduction in eggs and larvae by a pesticide application lasts just a few days, and the pesticide dramatically reduce s densities of many natural enemies along with eggs and larvae of H zea . In effect, this increases the role for insect pest control by the bats. Brazilian free tailed bats clearly play an important role in food production in the Winter Garden region of so uthcentral Texas. Our results suggest that conservation of bat habitat in this region is desirable on economic cost benefit grounds alone. In other regions of the world, bats also provide key services, such as seed dispersal and pollination of plants (Alle n Wardell et al . 1998). Yet the US Fish and Wildlife Service Threatened and Endangered Species Database lists only nine of the 45 bat species of the US as endangered. Cave ecosystems in general are under assault from guano mining, land development, polluti on, misguided vampire bat control attempts, prescribed burns in land management, vandalism, and impact from uninformed recreational cave explorers (Medellín 2003). Our ongoing research will extend this analysis to include all major bat colonies in the regi on, and to crops other than cotton in Mexico, Texas, and other states in the midwestern US that are beneficiaries of pest control by Brazilian free tailed bats. Acknowledgements This work was supported in part by grants from NSF (DBI 9808396 TH Kunz, P I and CJ Cleveland, Co PI) and (DBI 9988001 TH Kunz, PI, and MD Sorenson, Co PI), NSF (EIA 0326483 TH Kunz, PI, and M Betke, GF McCracken, P Morton, and W Westbrook, Co PIs), by the Bat Working Group (TH Kunz, GM McCracken, and CJ Cleveland, Co PIs) su pported by the National Center for Ecological Analysis and Synthesis, funded by a grant from NSF (DEB 0072909) to the University of California, Santa Barbara, by CONACYT grant G37425 V, CONACYT SEMARNAT grant 2002 C01 0357, and additional support by the P rogram for Conservation of Mexican Bats, the US Fish and Wildlife Service, National Fish and Wildlife Foundation, and the David and Lucille

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 125 Packard Foundation. Bat Conservation International (BCI), Texas Parks and Wildlife Depart ment, D . Bamberger, and Uni versidad Technical Monterrey supported earlier workshops on the economic value of bats. We thank J Ahlen, Y F Lee, S Petronio, M Rhodes, and P Schleider for assistance in gathering field data and data analysis. Bat Conservation International, R King, P Mor ton, J Pena, S Rafferty, T Reardon, C Schulze, L Sharp, the Texas Nature Conservancy, N Troxclair, B Walker, and K White provided valuable logistical or technical support. J Kennedy of BCI and the Texas Speleological Survey and B Keeley provided important data on cave and bridge localities. References Allen Wardell G, Bernhardt P, Bitner R, et al . 1998. The potential consequences of pollinator declines on the conservation of biodiversity and stability of food crop yields. Conserv Biol 12 : 8 17. Beerwinkle JD, Lopez JD Jr, Witz JA, et al . 1994. Seasonal radar and meteorological observations associated with nocturnal insectflight at altitudes to 900 meters. Ecol Entomol 23 : 676 83. Press. Davis RB, Her reid CF II, and Short HL. 1962. Mexican free tailed bats in Texas. Ecol Monogr 32 : 311 46. Gianessi LP and Anderson JE. 1995. Pesticide use in US crop production. Washington, DC: National Center for Food and Agricultural Policy. Kennedy GG and Margolies DC . 1985. Mobile arthropod pests: management in diversified agroecosystems. B Entomol Soc Am 31 : 21 27. Kovach J. 2003. Putting an environmental price to pesticide use. Paper presented at the 4th Integrated Pest Management Symposium, 4 8 April 2003, Indianap olis, IN. Kunz TH, Whitaker JO Jr, and Wadanoli MD. 1995. Dietary ener getics of the insectivorous Mexican free tailed bat ( Tadarida brasiliensis ) during pregnancy and lactation. Oecologia 101 : 407 15. Lee Y F and McCracken GF. 2005. Dietary variation of B razilian free tailed bats links to migratory populations of pest insects. J Mammal 86 : 67 76. Lee Y F and McCracken GF. 2002. Foraging activity and resource use of Brazilian free tailed bats Tadarida brasiliensis (Molossidae). Ecoscience 9 : 306 13. McCrack en GF. 2004. Estimates of population sizes in summer colonies of Brazilian free tailed bats ( Tadarida brasiliensis Monitoring trends in bat populations of the United States and territories: problems and prospects. Washin gton, DC: US Government Printing Office, US Geological Survey, Information and Technology Report 2003 0003. McCracken GF, Brown VA, Eldridge M, and Westbrook JK. 2005. The use of fecal DNA to verify and quantify the consumption of agricultural pests. Bat R es News 46 : 195 96. Medellín RA. 2003. Diversity and conservation of bats in México: research priorities, strategies, and actions. Wildlife Soc B 31 : 87 97. Pimentel D, Andow D, Dyson Hudson R, et al. 1991. Environmental and economic impacts of reducing U. S. agricultural pesticide use. In: D Pimentel (Ed). CRC Handbook of pest management in agriculture. Boca Raton, FL: CRC Press. Sansone C, Isakeit T, Lemon R, and Warrick B. 2002. Texas cotton production. Emphasizing integrated pest management. College Stat ion, TX: Texas Cooperative Extension Publication B 6116 Sansone CG and Smith JW. 2001. Natural mortality of Helicoverpa zea (Lepidoptera: Noctuidae) in short season cotton. Biol Control 30 : 113 22. Whitaker JO Jr. 1988. Food habits analysis of insectivorou s bats. In: TH Kunz (Ed). Ecological and behavioral methods for thestudy of bats. Washington, DC: Smithsonian Institution Press. Whitaker JO Jr, Neefus C, and Kunz TH. 1996. Dietary variation in the Mexican free tailed bat, Tadarida brasiliensis. J Mammal 77 : 716 24. Wiedenmann RN and Smith JW Jr. 1997. Attributes of natural enemies in ephemeral crop habitats. Biol Control 10 : 10 16. Williams TC, Ireland LC, and Williams JM. 1973. High altitude flights of the free tailed bat, Tadarida brasiliensis , observed with radar. J Mammal 54 : 807 21. Wolf WW, Westbrook JK, Raulston JR, et al . 1994. Radar detection of ascent of Heliocoverpa zea (Lepidoptera: Noctuidae) moths from corn in the lower Rio Grande Valley of Texas. In: Proceedings of the 13th International Con gress of Biometeorology, Calgary, Alberta, Canada. Woodward RT and Yong Suhk W. 2001. The economic value of wetland services: a meta analysis. Ecol Econ 37 : 257 70.

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 126 Bats Limit Arthropods and Herbivory in a Tropical Forest Margareta B. Kalka, 1 * Adam R. Smith, 1 Elisabeth K. V. Kalko 1,2 1 Smithsonian Tropical Research Institute, Apdo. 0843 03092, Balboa, Ancon, Panama. 2 Institute of Experimental Ecology, University of Ulm, Albert Einstein Allee 11, 89069 Ulm, Germany. *To whom correspon dence should be addressed. E mail: B ats are diverse and abundant insectivores that consume many herbivorous insects (1, 2). Insect herbivory, in turn, constrains plant reproduction and influences plant diversity and distribution (3). However, the impact of bat insectivory on plants has never been studied. Previous studies measuring top down reduction of insect herbivory focused on birds (4 6) but actually measured the combined impact of birds and bats because predator exclosures were left in place day and night. Partitioning the effects of each predator group is essential for both basic ecological questions, such as the top down maintenance of tropical diversity (3), and applied studies, such as th e biological control of agricultural pests (2, 6). We experimentally separated the ecological effects of insectivorous birds from those of insectivorous bats in a tropical lowland forest in Panama. We covered plants with mesh exclosures that permitted a c cess to arthropods but prevented birds or bats from gleaning them off of the plants. However, we left our exclosures in place only during the day or night, allowing us to compare arthropod abundance and herbivory on plants inaccessible to bats (nocturnal e xclosures, N = 42), plants inaccessible to birds (diurnal exclosures, N = 35), and uncovered controls (N = 43) in a randomized block design using five common understory plant species. We visually censused arthropods throughout the 10 week study to test the direct effect of treatment (i.e., absence of bats or birds) on insect and other arthropod abundance and measured leaf damage incurred during the study to test the indirect effect of treatment on herbivory (7). Nocturnal (bat) and diurnal (bird) exclosure s each directly increased arthropod abundance on plants, and nocturnal exclosures had a significantly stronger effect than diurnal exclosures (table S1 and Fig. 1A) [repeatedmeasures generalized linear model (GLM) treatment F 2,75 = 17.11, P < 0.001; all Tu significantly different (HSD) posthoc pairwise comparisons between treatments, P < 0.05]. Control plants averaged 4.9 ± 0.7 (SEM) arthropods per m 2 of leaf area per census; birdexclosed plants, 8.1 ± 1.0; and bat exclosed plants, 12.4 ± 1.6. Nocturnal and diurnal exclosures also each indirectly increased herbivory, and nocturnal exclosures again had a significantly stronger effect than diurnal exclosures (Fig. 1B; univariate GLMtreatment F 2,75 HSD posthoc pairw ise comparisons between treatments P < 0.005). Control plants averaged 4.3 ± 0.8% leaf area lost to herbivory; bird exclosed plants; 7.2 ± 1.6%; and bat exclosed plants, 13.3 ± 2.1% (7). Treatment effects on both arthropod abundance and herbivory were con sistent across plant species, and potential confounding variables such as light intensity, number of new leaves emerged during the study, and total leaf area neither differed between treatments nor interacted with treatment in either GLM (7). Fig. 1 . (A) Mean number of arthropods per m 2 per census. (B) Mean herbivory as percent of total leaf area. White bars represent controls (birds and bats present); yellow bars, diurnal exclosures (birds absent and bats present); and blue bars, nocturnal exc losures (bats absent and birds present); (Micronycteris microtis) consuming a katydid, Barro Colorado Island, Panama. [Photo: C. Ziegler]

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 127 Our data sug gest that bat predation both directly reduces arthropod abundance on plants and indirectly reduces herbivory. We also show that the ecological effects of insectivorous gleaning bats can be considerably stronger than those of birds. Our estimates of the dir ect and indirect impacts of both groups are likely conservative because (i) predation away from exclosures also reduces herbivory (2), (ii) very large arthropods may have been excluded along with bats and birds, (iii) predatory arthropods in the exclosures may have mitigated the effect of bird or bat exclusion (table S1), and (iv) topdown reduction of herbivory may be greater in the more productive forest canopy (5). Gleaning insectivorous bats are common in tropical and temperate lowland forests; thus, it is likely that bat predation of herbivorous insects reduces herbivory in the temperate zone as well (7). Given their ecological importance, bats should be included in future conservation plans aimed at preserving the integrity of tropical forests and also considered in agricultural management strategies based on natural pest control (2, 6). References and Notes 1. M. Kalka, E. K. V. Kalko, J. Trop. Ecol. 22, 1 (2006). 2. C. J. Cleveland et al., Front. Ecol. Environ. 4, 238 (2006). 3. P. V. A. Fine, I. Meso nes, P. D. Coley, Science 305, 663 (2004). 4. R. T. Holmes, J. C. Schultz, P. Nothnagle, Science 206, 462 (1979). 5. S. A. Van Bael, J. D. Brawn, S. K. Robinson, Proc. Natl. Acad. Sci. U.S.A. 100, 8304 (2003). 6. R. Greenberg et al., Ecology 81, 1750 (2000 ). 7. Materials and methods are available on Science Online. 8. M.B.K. was supported by STRI and Bat Conservation International, A.R.S. by SENACYT Panama, and E.K.V.K. by Deutsche Forschungemeinschaft Germany and STRI. S. A. van Bael and S. A. Mangan assis ted with experimental design and data analysis, respectively. Supporting Online Material Materials and Methods Table S1 References 26 November 2007; accepted 12 February 2008 10.1126/science.1153352

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 128 B ats Limit Insects in a Neotropical Agroforestry System Kimberly Williams Guillén, 1 * Ivette Perfecto, 1 John Vandermeer 1,2 T op down limitation of herbivores is an important ecosystem service that facilitates agricultural production (1). Several experimen ts in natural andmanaged ecosystems demonstrate the importance of avian predators in arthropod control (2). Although insectivorous bats are expected to have major impacts on arthropods (3), few studies have quantified the effects of bats on standing crops of arthropods. Because all previous exclosure based studies of avian insectivory have left exclosures up during the night, it is possible that a proportion of predation attributed to birdsmay represent predation by foliage gleaning bats. Here, we report an exclosure experiment conducted in a Mexican coffee agroforest, in which we directly measured the impact of predation by foliage gleaning birds and bats on arthropods found on coffee plants. We used exclosures made of agricultural netting erected around individual coffee plants in Finca Irlanda, an organic shade coffee plantation harboring abundant populations of 120 bird species and 45 bat species. We established 22 blocks of four treatments: birds only excluded (exclosure netting in place only during the day), bats only excluded (netting in place only during the night), both excluded (netting in place day and night), and control (no netting). We visually censused noncolonial arthropods (primarily insects, but also spiders, harvestmen, and mites) on all plants at the beginning of the experiments, every 2 weeks thereafter, and at the end of the experiment. We conducted the experiment for a 7 week period beginning January 2007 (dry season) and for an 8 week period beginning June 2007 (wet season). Exclusi on of birds and bats resulted in significant increases in total arthropods on experimental plants, although a significant amount of variation was also explained by foliage biomass and initial arthropod density (table S1). On average, total arthropod densit ies on plants from which both predators were excluded were 46% higher than those observed on control plants. There was a clear seasonal effect with regard to bats: Although bats did not have significant effects on arthropod densities in the dry season, the ir impacts were highly significant in the wet season, with an 84% increase in arthropod density in bat only exclosures, exceeding the effects of birds (Fig. 1). In neither season was there a significant interaction between bats and birds, indicating an add itive effect. Regardless of season, arthropod densities increased the most on plants from which both birds and bats were excluded (Fig. 1). These seasonal and additive patterns held for various arthropod taxa (table S2), although only birds significantly r educed spiders. Although predator exclusions resulted in increased arthropod density, no significant differences were seen between treatments in the prevalence or the intensity of leaf damage. At our site, bats were as important as birds in regulating ins ect populations across the course of the year. We suspect that increased impacts of birds in the dry season may result from an influx of insectivorous overwintering migrants from North America (4). We have no data on the absolute density of bats versus bir ds; however, at our site the capture rates (and presumably abundance) and reproductive activity of bats increased during the wet area may result in greater heat loss and concomitantly higher energy requirements (5), and energetic needs; thus, increased bat abundance and reproduction in the wet season may result in an increased impact of bat predation on understory Fig. 1. Mean number of arthropods ± SEM per 100 coffee leaves in four exclosure predators excluded ($). Numbers after treatment nam e in legends indicate mean number of arthropods ± SEM per 100 leaves across all counts. N = 88 for each season

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 129 arthropods. Our results are consistent with arguments that functional div ersity is central to the maintenance of ecosystem services (6). In this case, the presence of these two vertebrate taxa maintains a functional difference that enhances the efficacy of arthropod reduction. Previous exclosure studies have not differentiated between diurnal and nocturnal predators, attributing observed changes to birds. We suggest that these studies of the impacts have underestimated the importance of bats in limiting insects.Bat populations are declining worldwide (7), butmonitoring programs and conservation plans for bats lag far behind those for birds. Declining bat populations may compromise critical ecosystem services, making an improved understanding of their conservation status vital. References and Notes 1. G. C . Daily et al., Issues Ecol. 2, 2 (1997). 2. O. J. Schmitz, P. A. Hamback, A. P. Beckerman, Am. Nat. 155, 141 (2000). 3. C. J. Cleveland et al., Front. Ecol. Environ. 5, 238 (2006). 4. R. Greenberg, J. Avian Biol. 26, 260 (1995). 5. G. L. Graham, J. Biogeo gr. 17, 657 (1990). 6. D. Tilman et al., Science 277, 1300 (1997). 7. A. M. Hutson, S. P. Mickleburgh, P. A. Racey, Eds., Microchiropteran Bats: Global Status Survey and Conservation Action Plan [International Union for Conservation of Nature Species Survi val Commission (IUCN/SSC) Chiroptera Specialist Group, Gland, Switzerland, 2001]. 8. We thank G. Martínez and C. Rosas for field assistance and W. Peters for permission to work in Finca Irlanda. Research supported by NSF grant no. DBI 0610473 to K.W. G., B at Conservation International, and NSF grant no. DEB 0349388 to I.P. Supporting Online Material Tables S1 and S2 13 November 2007; accepted 12 February 2008 10.1126/science.1152944 BREVIA Table S1. Re sults of repeated measures factorial ANCOVA for the effects of bird predation, bat predation, season, and their interactions on the density of all non colonial arthropods on coffee plants, using number of leaves per plant and initial arthropod densities as covariates. N =88 for each season. * * All data ln(x+1) transformed prior to analysis. Repeated measures ANCOVA on total numbers of arthropods conducted using a 2° 2 factorial design with birds excluded (2 levels, birds present and birds excluded) and ba ts excluded (2 levels, bats present and bats excluded) as main effects; separate analyses were conducted for the wet and dry seasons. This design allows for testing of linear (additive or substitutive) versus nonlinear (synergistic or antagonistic) interac tions between predator types.

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 130 Placement of Nets for Bats: Effects on Perceived Fauna Steven K. Carroll 1 , Timothy C. Carter 1 , and George A. Feldhamer 1,2 1 Department of Zoology, Southern Illinois University, Carbondale, IL 62901 6501 (Current address of SKC: 4347 West Kenyon Avenue, Denver, CO 80236). 2 Corresponding author, . 2002 SOUTHEASTERN NATURALIST 1(2):193 198 ABSTRACT We used mist nets to survey bats at 41 sites throug hout the Shawnee National Forest in southern Illinois during the summers of 1999 and 2000. Unlike most previous studies, we placed nets in the interior of forest stands as well as the more typical placement along edge habitats associated with water. We cap tured 417 individual bats representing 10 species. Of these, 168 individuals (40.3%) and 8 species were collected in interior forest. Northern long eared bats ( Myotis septentrionalis ) were caught significantly more often in interior forest, whereas red bat s ( Lasiurus borealis ), eastern pipistrelles ( Pipistrellus subflavus ), and big brown bats ( Eptesicus fuscus ) were netted more often in edge habitats. In contiguous forest, especially within the geographic range of M. septentrionalis , a more accurate measure of bat diversity and relative abundance is obtained by placing nets in interior forest as well as edge habitats. INTRODUCTION Determination of bat community composition, species richness, diversity, and abundance is often important in formulating compre hensive forest management plans. The most direct method for surveying bats is to use capture methods such as mistnetting. Capture methods are also the only currently accepted methods for surveying endangered species. Capture data can be used to assess dive rsity and relative abundance of different bat species in a given region (Gardner et al. 1996, Jung et al. 1999, Kunz 1973, Lacki and Hutchinson 1999). Most mistnetting surveys focus on areas where capture success is traditionally highest, typically stream or flight corridors (Kunz and Kurta 1988). Placement of mistnets in interior forests is used less often because of perceived lower bat activity and therefore reduced capture success, and possible problems of accessibility. We used mistnets to determine su mmer distribution and relative abundance of bats in southern Illinois and their association with different habitat variables. We placed nets along roads or other habitat edges, in association with placement) , and in forest interiors we report on the importance of net placement on diversity and relative abundance of bat species that were captured. METHODS We sampled 41 sites in southern Illinois. Sites were primarily within Shawnee National Forest and were dominated by an overstory of oak ( Quercus spp.) and hickory ( Carya spp.). Sites were selected based on distance to a water source, size of surrounding contiguous forest, and accessibility. We amassed a total of 339 net nig hts during 80 nights from 18 May through 18 August 1999, and 12 May through 20 July 2000. Netting procedures followed the Indiana Bat Protocol (USFWS 1999). Generally, four net sets were used at a site. Two sets were placed over the nearest water source, n early all of which were intermittent or perennial streams or small rivers near roads or other edge habitats placement; Kunz and Kurta 1988). Two additional sets were placed in interior forest nets w ere placed 50 to 500 m from edge habitat. Netting sites were selected to represent a variety of understory cover and canopy closure. Nets were opened at dusk (approximately 2000 h) and monitored for 6 hours until 0200 h. Nets were checked for captured bats every 20 minutes.

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 131 We recorded the species, sex, age (juvenile/adult), reproductive status, mass, and forearm length of each captured bat. We used chisquare tests to analyze: 1) the selection of presumptive foraging habitat by comparing use by each specie s of bat (as determined by the number of captures of that species), versus the number of net sets in each habitat type (traditional vs. nontraditional); and 2) sex ratio of the total number of bats captured. A Shannon Wiener Diversity Index of bat captures was calculated for edge, interior, and total captures. RESULTS We captured 417 bats representing 10 species (Table 1) for an overall netting success of 1.23 captures per net night. A mean of 2.90 ± 0.72 species was captured at each site. There was no sig nificant difference between number of males (n = 211) and females (n = 206) 2 = 0.06, df = 1, P > 0.5). Seventy seven percent (n = 322) of all individuals captured were northern long eared bats ( Myotis septentrionalis , 41.7%), red bats ( Lasiurus borealis , 18.0%), or eastern pipistrelles ( Pipistrellus subflavus , 17.5%). These three species exhibited significant differences in habitat use. Northern long eared bats were captured in forest interior significantly more often than 2 = 26.6, d f = 1, P < 0.0001). Conversely, red bats were captured in 2 = 37.5, df = 1, P < 0.0001), 2 = 38.5, df = 1, P < 0.0001). Although sample sizes were smaller, we also captured big brown bats ( Eptesicus fuscus ) in edges significantly more 2 = 11.64, df = 1, P < 0.001). With the exception of southeastern bats ( Myotis austroriparius ) and silver haired bats ( Lasionycteris noctivagans ), all species captured in edge habitat were also ca ught in interior forest (Table 1). Species diversity of captured bats was close to 1.7 times higher in edge habitat than in interior habitat. DISCUSSION Of the 12 species of bats whose range includes Illinois (Hoffmeister 1989), we captured all but gray b ats ( Myotis grisescens ) and big eared bats ( Corynorhinus rafinesquii ). Our results differed from previous surveys for bats in Illinois and adjacent states (Clark and Clark 1987, Gardner et al. 1996, Hofmann et al. 1999, Kunz 1973, LaVal et al. 1977, Layne 1958), which report eastern pipistrelles, red bats, and big brown bats as the most common species. Northern long eared bats were routinely captured, but were never particularly abundant. In contrast, they were the most abundant species taken i n our study, comprising 41.7% of all individuals captured. Our results are more similar to those of Lacki and Hutchinson (1999) in northeastern Kentucky than to previous studies in Illinois. Differences in our capture results compared to other studies are likely due to our sampling methodology. Previous investigators (Clark and Clark 1987, Gardner et al. 1996, Hofmann et al. 1999, Kunz 1973) placing nets over perennial streams, roads, and trails used as flyways. This may limit sampling to bats that use open corridors; those species not using these habitats may be underrepresented. We suggest that populations of northern long eared bats may have been underestimated in previous research because of biased sampling effort. To accu rately sample an area for bats, By sampling a variety of habitat types in an area, a more accurate estimate of the bat fauna and the habitats used can be determined. Lacki and Hutchinson (1999) set nets in interior forest as well as edge; 70% of northern long eared bats they captured were in interior net sets. Our study showed similar results. Of 174 northern long eared bats captured, 121 (69.5%) were captured in inte rior forest. Furthermore, of the total 417 bats we captured, 168 (40.3%) were caught in the interior forest. Species diversity was lower in interior forest because of the large number of northern long eared bats captured when compared to the other seven sp ecies (Table 1). Given the extensive geographic range of northern long eared bats, future studies of bat community structure in eastern North America should include nets set in interior forest habitat. It is important to note that as many Indiana bats

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 132 ( My otis sodalis ), a federally endangered species, were caught with interior sets as were taken at edge sites. Without interior net sets we would have missed Indiana bats at 50% of netting locations. We captured relatively few hoary bats ( Lasiurus cinereus ) a nd silver haired bats ( Lasionycteris noctivagans ) (Table 1). We do not suggest, however, that these species are necessarily rare in Illinois. Mistnetting samples an extremely small area relative to that used by free flying bats, and foraging bats appear t o detect and avoid nets. Some species may not be represented because their normal flight activities are outside and Gannon 1999). Acoustic sampling of bat communities can detect the presence of those species t hat routinely fly at great heights or are otherwise beyond the sampling capabilities of Gannon 1999). However, because echolocation characteristics are very similar among some species, identification of bats to specie s level may not always be possible with acoustic sampling (Hart et al. 1993, Jung et al. 1999, Kalcounis et al. 1999). Mistnetting, including interior habitat, along with acoustic sampling should provide the most complete inventory of bat diversity. ACKNOWLEDGMENTS This study was part of Challenge Cost Share Agreement No. 98 0908 24 funded by the U.S. Forest Service, Shawnee National Forest. We thank Steve Widowski and Mike Spanel for their loan of equipment and support in all phas es of the project, and the numerous individuals who participated in mistnetting. LITERATURE CITED CLARK, B.K., and B.S. CLARK. 1987. Distribution notes of bats for westcentral Illinois. Transactions of the Illinois Academy of Science 80:207 212. GARDNER, J.E., J.E. HOFMANN, and J.D. GARNER. 1996. Summer distribution of the federally endangered Indiana bat ( Myotis sodalis ) in Illinois. Transactions of the Illinois State Academy of Science 89:187 196. HART, J.A., G.L. KIRKLAND, Jr., and S.C. GROSSMAN. 1993 . Relative abundance and habitat use by tree bats, Lasiurus spp., in southern Pennsylvania. Canadian Field Naturalist 107:208 212. HOFFMEISTER, D.F. 1989. Mammals of Illinois. University of Illinois Press, Urbana, IL. 348 pp. HOFMANN, J.E., J.E. GARDNER, J .K. KREJCA, and J.D. GARNER. 1999. Summer records and maternity roost of the southeastern myotis ( Myotis austroriparius ) in Illinois. Transactions of the Illinois State Academy of Science 92:95 107. JUNG, T.S., I.D. THOMPSON, R.D. TITMAN, and A.P. APPLEJOH N. 1999. Habitat selection by forest bats in relation to mixed wood stand types and structure in central Ontario. Journal of Wildlife Management 63:1306 1319. KALCOUNIS, M.C., K.A. HOBSON, R.M. BRIGHAM, and K.R. HECKER. 1999. Bat activity in the boreal for est: importance of stand type and vertical strata. Journal of Mammalogy 80:673 682. KUNZ, T.H. 1973. Resource utilization: temporal and spatial components of bat activity in central Iowa. Journal of Mammalogy 54:14 32. KUNZ, T.H., and A. KURTA. 1988. Cap ture methods and holding devices. Pp. 1 30, In T. H. Kunz (Ed.). Ecological and Behavioral Methods for the Study of Bats. Smithsonian Institution Press, Washington, DC. 533 pp. LACKI, M.J. and J.T. HUTCHINSON. 1999. Communities of bats (Chiroptera) in the Greyson Lake Region, northeastern Kentucky. Journal of the Kentucky Academy of Science 60:9 15. LaVAL, R.K., R.L. CLAWSON, M.L. LaVAL, and W. CAIRE. 1977. Foraging behavior and nocturnal activity patterns of Missouri bats, with emphasis on the endangered species Myotis grisescens and Myotis sodalis . Journal of Mammalogy 58:592 599. LAYNE, J.N. 1958. Notes on mammals of southern Illinois. American Midland Naturalist 60:219 254. comparison of acoustic versus capture techniques for the inventory of bats. Journal of Mammalogy 80:24 30. UNITED STATES FISH AND WILDLIFE SERVICE. 1999. Agency draft Indiana bat ( Myotis sodalis ) revised recovery plan. Region 3, United States Fish and Wildlife Service, Ft. Snelling, MN. 53 pp

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 133 Mist Net Effort Required to Inventory a Forest Bat Species Assemblage Theodore J. Weller , 1 Pacific Southwest Research Station, United States Department of Agriculture, Forest Service, 1700 Bayview Drive, Arcata, CA 95521, USA Danny C. Lee , 2 Pacific Sout hwest Research Station, United States Department of Agriculture, Forest Service, 1700 Bayview Drive, Arcata, CA 95521, USA 1 E mail: 2 Present address: United States Department of Agriculture, Forest Service, Southern Research Station, P .O. Box 2680, Asheville, NC 28802, USA ABSTRACT Little quantitative information exists about the survey effort necessary to inventory temperate bat species assemblages. We used a bootstrap re sampling algorithm to estimate the number of mist net surveys required to capture individuals from 9 species at both study area and site levels using data collected in a forested watershed in northwestern California, USA, during 1996 2000. The mean number of simulated surveys required to capture individual species va retrospectively evaluated strategies to reduce required survey effort by sub sampling data from 1996 to 1998 and tested the strategies in the field during 1999 and 2000. Using data from 1996 to 1998 , the mean number of simulated surveys required to capture 8 out of 9 species was 26.3, but a 95% probability of capture required .61 surveys. Inventory efficiency, defined as the cumulative proportion of species detected per survey effort, improved for bo th the study area and individual sites by conducting surveys later in summer. We realized further improvements in study area inventory efficiency by focusing on productive sites. We found that 3 surveys conducted between 1 July and 10 September at each of 4 productive sites in this 10 km 2 study area resulted in the capture of 8 species annually. Quantitative estimation of the survey effort required to assess bat species occurrence improves the ability to plan and execute reliable, efficient inventories. Re sults from our study should be useful for planning inventories in nearby geographical areas and similar habitat types; further, the analytical methods we used to assess effort are broadly applicable to other survey methods and taxa. JOURNAL OF WILDLIFE M ANAGEMENT 71(1): 251 257; 2007. DOI: 10.2193.2005 384 KEY WORDS : bats, inventory, species accumulation, species richness, survey effort, survey protocol. Bats are important components of biodiversity that are often underrepresented in conservation and m anagement plans because of a lack of information on population status and habitat requirements (Pierson 1998, Richards and Hall 1998). Nevertheless, increased interest in bats (Fenton 1997) coupled with their status as species of concern in many areas (Bog an et al. 1996) has increased the number of inventories aimed at documenting species occurrence (Weller and Zielinski 2006). To date, this work has often been conducted with little guidance (but see Resources Inventory Committee 1998, Vonhof 2002) or evalu ation of the survey effort required to conduct an accurate inventory. In planning an inventory, an important question is the number of surveys required to detect species with a given level of confidence (Zielinski and Stauffer 1996, Ke´ry 2002, Sherwin et al. 2003). Studies of other taxa have evaluated the spatial and temporal replication and survey duration necessary to estimate abundance and establish trends over time (Link et al. 1994, Lewis and Gould 2000, Thompson et al. 2002, Watson 2004) or to estim ate number of species detected with increasing effort (Bury and Corn 1987, Block et al. 1994). Evaluations of survey effort necessary to describe bat species assemblages are limited to Australia and the Neotropics (Mills et al. 1996, Moreno and Halffter 20 00, Aguirre 2002, Bernard and Fenton 2002). A similar assessment of survey effort has not been made for temperate bat assemblages of North America or Europe despite a large number of surveys conducted in these areas. Estimates of survey effort required to document tropical bat species assemblages provide little guidance for inventories in temperate areas because of differences in species, habitats, and objectives. Tropical areas generally

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 134 support a larger number of lesser known bat species, and a frequent o bjective is to compare the numbers of species present among areas of conservation concern. Hence, the relevant metric for many tropical inventories is the number of species detected for a given level of effort and is frequently addressed using species accu mulation curves (Moreno and Halffter 2000, Estrada and Coates Estrada 2001, Aguirre 2002, Bernard and Fenton 2002). In temperate areas where the bat fauna generally comprises fewer, better known species, questions regarding survey effort are typically go al oriented and may focus on efficiency of survey effort. Relevant questions include 1) given a goal of detecting species X, how many surveys are required? or 2) given a goal of detecting Y% of the species in an area, how many surveys should be conducted? Such questions have not been addressed for a temperate bat assemblage and, though conventional species accumulation curves can provide post hoc assessments of survey completeness, they do not do so in a predictive manner. Activity patterns of temperate bats vary greatly both spatially and temporally (Hayes 1997, 2000). Consequently, multiple surveys are needed to detect individual species and an even greater number to detect all species that use an area. Given limited resources, it is imperative that inv entories are both accurate (species are detected and correctly identified) and efficient (measured by species detected/survey). Where as accuracy can be improved simply by increasing the number of surveys (White 2004), the greater challenge is to do so effi ciently. We examined sampling accuracy and efficiency using results from mist net surveys conducted in a forested watershed in northern California, USA. Our goals were to quantify the survey effort necessary to inventory the summer bat species assemblage a nd evaluate practical measures to improve efficiency of inventories in this area. STUDY AREA Our study area was within the Pilot Creek watershed in the Six Rivers National Forest in northwestern California (40837 0 N, 123836 0 W). The watershed was approximat ely 55 km from the Pacific Ocean at an elevation range of 950 1,320 m. This area was characterized by steep, rugged terrain, commonly gaining 200 m in elevation for each kilometer of distance. This 100 km 2 watershed had hundreds of small tributaries, but only Pilot Creek and the lower reaches of its larger tributaries maintained surface flows throughout summer. Sixty percent of the watershed was late successional forest, including the headwaters area where our study took place. Vegetation was dominated by Douglas fir ( Pseudotsuga menziesii ), but white fir ( Abies concolor ) and oaks ( Quercus chrysolepis, Q. kelloggii , and Q. garryana ) were also common. There were no known caves, mines, bridges, or buildings in our study area. The nearest weather station was approximately 20 km away at the Mad River Ranger Station (elevation 846 m). Mean annual precipitation during the study was approximately 195 cm, of which 2.0 cm accumulated from June through August. Mean minimum temperatures for June, July, and August wer e 7.28 C, 9.48 C, and 8.98 C, respectively; mean maximum temperatures were 25.98 C, 30.28 C, and 30.48 C, respectively. METHODS We attempted to capture bats in mist nets at water sources and along suspected flight corridors during their summer activity pe riod. We defined a survey as a single night of mist netting at a site. We selected suitable mist net sites that spanned a variety of habitats used by bats, with the goal of maximizing number of species captured in the study area. We conducted surveys to me et the needs of our and 2 other studies (Seidman and Zabel 2001, Weller and Zabel 2001). During 1996 1998 (period 1), we surveyed 9 17 sites per year during June September (Table 1). In total, we surveyed 28 different

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 135 sites including 12 sites along Pilot C reek, 2 along perennial tributaries to Pilot Creek, 10 on intermittent streams, 2 on roads, one at a pond, and one at a meadow edge. All survey sites fell within a 9.8 km 2 polygon in the upper half of the watershed. During period 1, we conducted surveys at sites where we suspected capture efforts to be successful and subsequently revisited sites where we captured multiple species or individuals. Such an approach is commonly used to document species presence in an area and we refer to it as conventional meth ods. By the end of 1997, we had identified 4 sites that were particularly effective. Subsequently, we conducted a disproportionate number of surveys at these sites, which we refer to as focal sites. Three of the focal sites were along Pilot Creek, spaced 5 70 m and 3.7 km apart; the fourth focal site was at an intermittent stream. We chose the number, length, and configuration of nets to suit the physical characteristics of each site. Mist nets were 2.6 m high and ranged in length from 6 to 12 m. We used a n average of 3.6 nets per survey (SD 1/4 0.8, range 1/4 2 6). Surveys began at sunset and continued for a minimum 3 hours or until an hour passed after the last bat was captured, whichever was longer. We conducted surveys regardless of temperature but not during periods of precipitation. Mean temperature at survey end was 13.08 C (SD 1/4 3.58 C, range 1/4 6.0 24.58 C). We used survey results from period 1 to explore some of the spatial and temporal effects on survey effort required to capture individual a nd multiple species of bats. Using all surveys from period 1, we estimated number of annual surveys required to 1) first capture each species and 2) cumulatively detect multiple species. We then evaluated strategies for reducing annual survey effort by com paring these results to several subsets of these data: 1) surveys conducted after 30 June (post Jun), 2) surveys conducted after 31 July (post Jul), and 3) surveys at focal sites during these date ranges. We selected 30 June to approximate the end date of low nighttime temperatures that can depress bat activity (Maier 1992, Hayes 1997, Erickson and West 2002); 31 July approximated the date when we first captured

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 136 juveniles. The presence of volant juveniles can increase the number of individuals of a species active in an area (Maier 1992, Schulz 1999) and consequently improve chances of capturing those species. We applied strategies that appeared effective based on results from period 1 in the field during 1999 and 2000 (period 2) to evaluate their applicabili ty. Additionally, we used results of focal site surveys to evaluate the effort required to assess species richness at individual sites. We sampled from the complete set of surveys conducted at each focal site from 1996 to 2000 to estimate the number of su rveys necessary to accumulate species at the site level. We also compared the number of species captured at individual sites using the full data set to post June and post July surveys. We generated bootstrap estimates (sensu Efron and Tibshirani 1993) of the number of surveys required to meet each objective by randomly drawing from data pools created by sub setting the original data set based on when surveys were conducted and whether all sites or only focal sites were included. The bootstrap routine drew surveys, with replacement, from each pool of surveys and recorded the number of simulated surveys until a particular species was first captured or a specified number of species was captured. When number of species captured was the objective, we made random draws until all species in the pool of surveys were present in the simulated sample. Because a single draw included the complete species assemblage captured at a single site and date combination, interspecific correlations in occurrence were maintained in the bootstrap samples. We generated summary statistics from the distribution of 10,000 samples from each data pool. We conducted sampling and summary statistics using SAS Release 8.1 (SAS Institute, Cary, NC). RESULTS We captured 11 species of bats in 13 5 surveys over 5 years (Tables 1, 2). We captured 2 species ( Myotis lucifugus and Lasiurus blossevilli ) only in 1998; we omitted these species from the 9 core species (sensu Magurran and Henderson 2003) analyzed here. When we included all surveys from 1996 to 2000 in the pool, the mean number of simulated surveys required to first detect a species ranged from 1.5 surveys for M. californicus to 44.9 surveys for L. cinereus . The 95th percentile, which corresponds to the estimated number of simulated surveys r equired to ensure a 95% probability of capture, varied from 3 to 136 surveys for those 2 species (Fig. 1). The mean number of simulated surveys required to cumulatively capture all 9 core species was 53 surveys; achieving a 95% probability of capturing the core species would have required 138 surveys (Fig. 2). By comparison, despite up to 47 surveys per year, we captured _8 core species in the field annually (Tables 1, 2). Using the data pool from period 1, when we used conventional methods, a mean of 26.3 simulated surveys were required to cumulatively capture 8 of the core species and 61 surveys were required to achieve a 95%probability of capturing those species. The number of surveys required to first capture each individual species was reduced by inclu ding only post June surveys and further reduced by including only post July surveys in nearly every case (Table 3). Similarly, including only post June or post July surveys decreased by 18% the mean number of simulated surveys needed to capture 8 species. The simulated effort necessary to cumulatively capture 7 of the core species decreased 16% using post June data and 29% using post July data (Table 3). Pooling only focal site surveys over all dates reduced the mean number of simulated surveys required to first detect all but 1 individual species ( M. yumanensis ) during period 1 (Table 3). The increase in simulated effort required to cumulatively capture 8 core species by surveying focal sites in period 1 was due to the large number of surveys until the fir st capture of M. yumanensis . By contrast, the simulated effort to capture 6 and 7 species using focal sites in period 1 decreased by 17%and 19%, respectively, when compared to surveys at all sites (Table 3). Using the data pool from post June surveys at focal sites during period 1 reduced the simulated number of surveys required to capture each species when compared to focal site surveys from all dates and for all species except M. yumanensis when compared to post June surveys at all sites (Table 3). Howe ver, the simulated number of surveys required to capture 3 individual species ( C. townsendii, L. noctivagans , and M. yumanensis ) and to cumulatively capture 7 and 8 core species was greater using post July than post June surveys at focal sites (Table 3). We applied these findings in the field during period 2, when we surveyed each focal site 3 times per year post June (Table 1). Despite conducting only 12 annual surveys, we captured 8 core species in the field during both years (Table 2). Among the 7 core species that we captured in both period 1 and period 2, the simulated effort necessary to capture all but one species ( L.

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 137 noctivagans ) was less in period 2 (Table 3). The mean number of simulated surveys in period 2 required to cumulatively capture 8 core species was 46% as much as the effort required for all sites and dates in period 1. The 95th percentile for the simulated number of surveys required to cumulatively capture 8 species was reached in 26 surveys in period 2 compared to 61 surveys in period 1 (43% of the effort). The strategy used during period 2 was also more efficient at detecting commonly captured species; the mean number of simulated surveys to accumulate 6 species was 71% of that required in period 1 (Table 3) and the simulated effort requ ired to achieve 95% probability of capturing 6 species was 9 surveys in period 2 compared to 14 surveys in period 1 (64% of the effort). Sampling from the pool of post July surveys from period 2 reduced the simulated number of surveys required to accumulat e 6 8 species but had mixed effects on individual species when compared to the full set of surveys from period 2 (Table 3). We conducted 17 field surveys at each of 3 focal sites and 21 surveys at the other focal site between 1996 and 2000. We captured 8 core species at each of the 3 sites along Pilot Creek and 5 core species at the upland site. The simulated mean number of surveys required to capture 8 core species at the 3 sites along Pilot Creek was 18.5 and ranged from 14.1 to 27.2 surveys among the 3 sites. Capture of 7 species required a mean of 9.2 (range1/47.3 12.3) simulated surveys. Capture of 8 core species at the 3 focal sites along Pilot Creek required a mean of 15.9 (range1/412.7 22.7) post June simulated surveys and 14.2 (range 1/4 13.1 15.9 ) post July surveys. Capture of 5 species at the upland site required a mean of 25.7 simulated surveys. DISCUSSION Survey effort necessary to capture bats varied by species, sites surveyed, and time periods over which we conducted surveys. Although we cap tured the most common species with relatively modest survey effort, pursuit of uncommon species precipitated a sharp rise in required effort. Studies in reconnaissance. Of course, identification of focal sites required a preliminary phase of sampling to id entify the most successful sites. When pilot studies are not practical, surveying additional sites, rather than repeated surveys at existing sites, is a more effective inventory strategy for uncommon species (Colwell and Coddington 1994, MacKenzie and Royl e 2005). Despite averaging 4 10 individuals and 2 3 species per survey, each of the 4 focal sites had _1 survey in which we only captured one bat. Even during the most productive periods (i.e., after 31 Jul) .14 mist net surveys were required to capture a ll species that occurred at an individual site within this study area. This is similar to the number of mist net surveys required to capture up to 18 species within small habitat patches in tropical Mexico (Moreno and Halffter 2000). By contrast, it has be en reported that species richness at a site can be adequately described with 2 3 surveys using bat detectors in Europe (Ahle´n and Baagøe 1999) or harp traps in Australia (Mills et al. 1996). Note also that the level of effort necessary to capture species occurring at an individual site approached that required to capture species in the entire study area. Similar results were found in inventories of bats in Mexico (Moreno and Halffter 2000) and Martes in California (Zielinski and Stauffer 1996), where the e ffort necessary for a reliable inventory of an individual stratum approached or

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 138 exceeded the effort necessary to inventory a larger area comprising multiple strata. This may be because study area inventories incorporate both spatial and temporal replicatio n through the use of multiple survey sites, whereas a site inventory can only include temporal replication. As with other analytical methods (e.g., species accumulation curves), assessment of inventory completeness and strategies for improving efficiency in our study required an initial survey effort to generate a pool of sample data with which to work. Conventionally, inventory effectiveness has been inferred from species accumulation curves by inspection for inflection points that indicate a decrease in returns Estrada and Coates Estrada 2001). In systems with greater species richness, models were fit to species accumulation curves to estimate the number of species expected in an area and inventory completen ess was assessed based on detection of a given proportion (e.g., 90%) of the expected species (Sobero´n and Llorente 1993, Flather 1996, Moreno and Halffter 2000). In our study, rather than determine the number of species detected for a given level of effo rt, we asked how much effort was required to confidently detect a given species or number of species. Hence, the relationship between species detected and survey effort in our study (Fig. 2) is the inverse of conventional species accumulation curves. Addi tionally, our approach provides a probability based approach to inventory planning and evaluation. Thresholds for proportion of the species assemblage to target can be set a priori in order to identify the number of surveys that might be necessary to meet objectives. For instance, the number of surveys necessary to achieve a 95%probability of capturing a specified number of species could be prescribed as minimum required survey effort. Estimates of required survey effort can simplify planning and allow info rmed tradeoffs between inventory accuracy and resources available to conduct work. For instance, simulations indicated that capture of 8 of the 9 core species in our study required less than half of the effort necessary to capture all 9 species. If detecti on of 7 of the core species was considered sufficient, this could be accomplished with a 50 70% further reduction in effort (Table 3). Our analytical approach also quantifies survey effort necessary to capture individual species when, as in most temperate areas, it is more important to establish which species, rather than how many species, are present (Watson 2004). Establishing the probability of capture or detection with a given level of effort provides a defensible means of quantifying whether sufficien t effort has been applied to detect a species, given that it is present (Zielinski and the Neotropics, where number of species and diversity of habitats were greater, have required 18 70 mist net surveys to capture 90% of the estimated species richness (Mo reno and Halffter 2000, Aguirre 2002, Bernard and Fenton 2002). Hence, we were surprised that, using conventional methods, .26 surveys were required to capture 8 of the 9 core species in our relatively small, vegetatively homogenous, study area. This level of spatiotemporal replication was necessary to compensate for our incomplete understanding of the relationship between bat activity and a number of biotic and abiotic factors including weather conditions, insect availability, and reproductive condition of bats (Maier 1992, Hayes 1997, Erickson and West 2002). Additionally, all bats in our study are in the family Vespertilionidae, which are reportedly difficult to capture using mist nets (Kalko 1998, Moreno and Halffter 2000); this may help explain why the levels of effort we observed were comparable to those in Neotropical study areas. Because the level of effort required to capture uncommon species of bats may exceed the means of some biologists (Weller and Zielinski 2006), it is important to elucidate st rategies for improving survey efficiency. In our study area, conducting surveys later in the summer and focusing efforts on the most productive sites reduced the number of surveys required to meet inventory objectives. Although post June surveys consistent ly reduced effort required to achieve inventory objectives, post July surveys produced mixed results, perhaps as a result of too few total survey nights remaining to capture some species. We generated a relatively complete inventory of the species in our s tudy area using a density of approximately 4 focal sites/10 km 2 . Compared to surveying sites of unknown quality, limiting surveys to focal sites improved the rate of species accumulation, saved time, and simplified logistics by eliminating additional site Stauffer 1996, Ke´ry 2002, Sherwin et al. 2003). Future projects in nearby areas and similar habitats could use our estimates of sample effort for planning purposes when designing inventories for individual species. However, caution must be exercised when applying our estimates elsewhere because they result from work in a single study area. Similar analytic methods should be applied to data from multiple study areas before meaningful conclusions about capture probabilities, and their

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 139 variability, for indivi dual species can be made. Our estimates of required survey effort were based solely on results of mist net surveys. Several studies have concluded that a combination of mist net and acoustic monitoring surveys provide more complete bat inventories than em ploying one or the other technique alone (Kuenzi and Morrison 1998, Murray et al. 1999, acoustic methods in our study likely would have decreased the number of surveys required to document the presence of some species at both the site and study area level. However, because some species are difficult to detect or identify from their echolocation calls capture surveys will continue to be a vital component of bat inventories; and quantifying the effort necessary to do so reliably is important. Further, the analytical approach demonstrated here for assessing required mist net survey effort could be profitably applied to quantify survey effort for other (e.g., a coustic) inventory techniques. MANAGEMENT IMPLICATIONS We demonstrated that multiple mist net surveys are necessary to capture most species of bats in a forested area. The strategies we identified for improving inventory efficiency, such as conducting sur veys later in the summer and focusing survey effort on productive sites, are likely to be effective in similar habitats and nearby geographic areas, but should be validated first. The goal oriented analysis of survey effort we introduced is broadly applica ble to evaluate completeness and improve efficiency of inventories conducted in other areas, using other survey methods, and for other taxa. ACKNOWLEDGMENTS We thank C. Zabel for her initiation and oversight of our work. V. Seidman directed most of the da ta collection in 1996 and 1997. B. Hill, J. Moore, and A. Miles made significant contributions to completion of the field work. Reviews of earlier drafts by J. Baldwin, A. Kuenzi, P. Ormsbee, and W. Zielinski improved the manuscript. Our work was funded by the Pacific Southwest Research Station, United States Department of Agriculture, Forest Service. LITERATURE CITED Aguirre, L. F. 2002. Structure of a Neotropical savanna bat community. Journal of Mammalogy 83:775 784. Ahle´n, I., and H. J. Baagøe. 1999. Use of ultrasound detectors for bat studies in Europe: experiences from field identification, surveys, and monitoring. Acta Chiropterologica 1:137 150. Bernard, E., and M. B. Fenton. 2002. Species diversity of bats (Mammalia: Chiroptera) in forest fragment s, primary forests, and savannas in central Amazonia, Brazil. Canadian Journal of Zoology 80:1124 1140. Block, W. M., M. L. Morrison, J. Verner, and P. N. Manley. 1994. Assessing wildlife habitat relationship models: a case study with California oak woodla nds. Wildlife Society Bulletin 22:549 561. conservation of bats in North America. Endangered Species Update 13:1 14. Bury, R. B., and P. S. Corn. 1987. Evaluation of pitfall trapping in northwest ern forests: trap arrays with drift fences. Journal of Wildlife Management 51:112 119. Colwell, R. K., and J. A. Coddington. 1994. Estimating terrestrial biodiversity through extrapolation. Philosophical Transactions of the Royal Society of London 345:101 118. Duffy, A. M., L. F. Lumsden, C. R. Caddle, R. R. Chick, and G. R. Newell. 2000. The efficacy of Anabat ultrasound detectors and harp traps for surveying microchiropterans in south eastern Australia. Acta Chiropterologica 2:127 144. Efron, B., and R. J . Tibshirani. 1993. Introduction to the bootstrap. Chapman and Hall, New York, New York, USA. Erickson, J. L., and S. D. West. 2002. The influence of regional climate and nightly weather conditions on activity patterns of insectivorous bats. Acta Chiropter ologica 4:17 24. Estrada, A., and R. Coates Estrada. 2001. Species composition and reproductive phenology of bats in a tropical landscape at Los Tuxtlas, Mexico. Journal of Tropical Ecology 17:627 646. Fenton, M. B. 1997. Science and the conservation of ba ts. Journal of Mammalogy 78:1 14. Flather, C. H. 1996. Fitting species accumulation functions and assessing regional land use impacts on avian diversity. Journal of Biogeography 23: 155 168. Hayes, J. P. 1997. Temporal variation in activity of bats and the design of echolocation monitoring studies. Journal of Mammalogy 78:514 524. Hayes, J. P. 2000. Assumptions and practical considerations in the design and interpretation of echolocation monitoring studies. Acta Chiropterologica 2:225 236. Kalko, E. K. V. 1 998. Organisation and diversity of tropical bat communities through space and time. Zoology 101:281 297. Ke´ry, M. 2002. Inferring the absence of a species a case study of snakes. Journal of Wildlife Management 66:330 338. Kuenzi, A. J., and M. L. Morrison . 1998. Detection of bats by mist nets and ultrasonic sensors. Wildlife Society Bulletin 26:307 311.

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 140 Lewis, S. A., and W. R. Gould. 2000. Survey effort effects on power to detect trends in raptor migration counts. Wildlife Society Bulletin 28: 317 329. Lin k, W. A., R. J. Barker, and J. R. Sauer. 1994. Within site variability in surveys of wildlife populations. Ecology 75:1097 1108. MacKenzie, D. I., and J. A. Royle. 2005. Designing occupancy studies: general advice and allocating survey effort. Journal of A pplied Ecology 42: 1105 1114. Magurran, A. E., and P. A. Henderson. 2003. Explaining the excess of rare species in natural species abundance distributions. Nature 422:714 716. Maier, C. 1992. Activity patterns of pipistrelle bats (Pipistrellus pipistrellus ) in Oxfordshire. Journal of Zoology 228:69 80. Mills, D. J., T. W. Norton, H. E. Parnaby, R. B. Cunningham, and H. A. Nix. 1996. Designing surveys for microchiropteran bats in complex forest landscapes a pilot study from south east Australia. Forest Ecolo gy and Management 85:149 161. Moreno, C. E., and G. Halffter. 2000. Assessing the completeness of bat biodiversity inventories using species accumulation curves. Journal of Applied Ecology 37:149 158. Murray, K. L., E. R. Britzke, B. M. Handley, and L. W. Robbins. 1999. Surveying bat communities: a comparison between mist nets and the Anabat II bat detector system. Acta Chiropterologica 1:105 112. acoustic versus capture techniques for the inventory of bats. Journal of Mammalogy 80: 24 30. Pierson, E. D. 1998. Tall trees, deep holes, and scarred landscapes: conservation biology of North American bats. Pages 309 325 in T. H. Kunz and P. A. Racey, editors. Bat biology and conservation. Smithsonian Insti tution, Washington, D.C., USA. Richards, G. C., and L. S. Hall. 1998. Conservation biology of Australian bats: are recent advances solving our problems? Pages 271 281 in T. H. Kunz and P. A. Racey, editors. Bat biology and conservation. Smithsonian Institu tion, Washington, D.C., USA. Resources Inventory Committee. 1998. Inventory and monitoring methods for bats. Standards and Components Environment and Parks, Victoria, British Columbia, Canada. ,http: // assets/bats.pdf.. Accessed 25 Aug 2006. Schulz, M. 1999. Relative abundance and other aspects of the natural history of the rare golden tipped bat, Kerivoula papuensis (Chiroptera: Vespertilionidae). Acta Chirop terologica 1:165 178. Seidman, V. M., and C. J. Zabel. 2001. Bat activity along intermittent streams in northwestern California. Journal of Mammalogy 82:738 747. Sherwin, R. E., W. L. Gannon, and J. S. Altenbach. 2003. Managing complex systems simply: unde rstanding eared bat. Wildlife Society Bulletin 31:62 72. Sobero´n, J., and J. Llorente. 1993. The use of species accumulation functions for the prediction of species richness. Conservation Biology 7 : 480 488. Thompson, F. R., III, D. E. Burhans, and B. Root. 2002. Effects of point count protocol on bird abundance and variability estimates and power to detect population trends. Journal of Field Ornithology 73:141 150. Vonhof, M. J. 2002. Handbook of i nventory methods and standard protocols for surveying bats in Alberta. Report prepared for Alberta Environment, Edmonton, Canada. Watson, D. M. 2004. Comparative evaluation of new approaches to survey birds. Wildlife Research 31:1 11. Weller, T. J., and C. J. Zabel. 2001. Characteristics of fringed myotis day roosts in northern California. Journal of Wildlife Management 65:489 497. Weller, T. J., and W. J. Zielinski. 2006. Using an Internet questionnaire to characterize bat survey efforts in the United Sta tes and Canada. Wildlife Society Bulletin 34:1000 1008. White, E. P. 2004. Two phase species time relationships in North American land birds. Ecology Letters 7:329 336. Zielinski, W. J., and H. B. Stauffer. 1996. Monitoring Martes populations in California : survey design and power analysis. Ecological Applications 6:1254 1267. Associate Editor: Szewczak

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 141 An Improved Trap for Bats by Merlin D. Tuttle J. Mamm., 55(2): 475 477, 1974. Numerous methods of collecting bats have been dev eloped, the most important of which are summarized by Constantine (1958: 17) and by Greenhall and Paradiso (1968: 8 19). Most of these are useful only under relatively restricted conditions. Even the widely requires constant attention, soon becomes damaged, and entangles bats to such an extent that rapid handling of large numbers is impossible. Constantine (1958) first described t require excessive labor for the removal of captured bats. His original trap, which caught more than 45,000 free tailed bats, was too bulky for general use, but modifications (Constantine, 1958; 1962; 1969) produced smaller, folding traps, which were easi ly transported by two men. Each of rectangular frame, supporting fine vertical wires spaced at one inch intervals and kept taut. These traps proved satisfactory for vampires and for fast flying free tailed bats, bu t were not generally useful in capturing other species. In order to trap efficiently the highly maneuverable vespertilionid and emballonurid bats, I have developed a trap, which employs a double frame and other modifications. This trap is easily portable by one man and can be assembled or broken down in 45 minutes. It can be used under a wide range of conditions and has proven successful in capturing many temperate and tropical species. The trap consists of two rectangular frames held two inches apart by four 3/4 inch (.64 centimeters, cm) threaded steel rods (Fig. 1a). The sides of the frames consist of aluminum tubes (inside diameter, 29 millimeters, mm; outside diameter, 32 mm) 72 inches (182.9 cm) long. A hole is drilled 1 1/4 inches (3.2 cm) from eac h end of each tube for bolting the frame together (Fig. 1b), and two more located 3 1/4 and 4 1/4 inches (8.3 and 10.8 cm) up from the base on each side are for attachment of the bag support plates (Fig. le). The extra set of holes allows for vertical adju stment of the bag. Additional holes are drilled 22 3/4 and 27 3/4 inches (57.8 and 70.5 cm) from the base to allow for attachment of legs (Fig. 1d). The upper and lower ends of each frame are identical, consisting of two 62 inch (157.5 cm) lengths of alum inum tubing (inside diameter, 2.5 cm; outside diameter, 2.8 cm). The ends of each tube are cut at 45 degrees, and a 6 inch (15.2 cm) length of the same size of tubing is welded at that angle (Fig. 1b). The end pieces are drilled to match the holes previous ly drilled in the sides into which they telescope and are bolted. Holes are drilled 5 1/4 and 21 1/2 inches (13.3 and 54.6 cm) from each end (Fig. 1b) for support of

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 142 the aluminum angle to which the wires are attached. For attachment of wire strands a secti on of angled aluminum 59 inches (149.9 cm) long is drilled to match the holes already present in the frame (Fig. 1b). One section is bolted to the base whereas the other is attached to the top by means of four 5 inch (12.7 cm) threaded steel rods (Fig. 1b) , which allow for adjustment of wire tension. Prior to installation on the frame the angled sections are drilled at 1 inch (2.5 cm) intervals to allow for attachment of wires (Fig. 1b). Receptacles for the legs are formed by welding 10 1/2 and 4 1/4 inch (26.7 and 10.8 cm) pieces of aluminum tubing (inside diameter, 2.9 cm; outside diameter 3.2 cm) together at an angle of 80 degrees (Fig. 1d). Each 10½ inch (26.7 cm) section is drilled 3 1/4 and 8 1/4 inches (8.3 and 21.0 cm) from its upper end, allowing f or attachment to the frame (Fig. 1d). A hole is drilled on the inner side of the 4 1/2 inch (11.4 cm) section 1 1/4 inches (3.2 cm) from the lower end, and a 1/4 inch (.64 cm) nut is welded over the hole (Fig. 1c). Each leg consists of two 36 inch (91.4 cm ) sections of telescoping aluminum tubing (inside diameter, 2.5 cm; outside diameter, 2.8 cm fitting over inside diameter, 2.0 cm; outside diameter, 2.2 cm). The outer section is drilled 2 1/4 inches (5.7 cm) from one end, and a 1/4 inch (.64 cm) nut is we lded over the hole (Fig. 1c). The legs are attached to the leg receptacles and adjusted for length by use of thumb bolts (Fig. 1c). The canvas bag is 25 inches (63.5 cm) deep by 60 inches (152.4 cm) long and 14 inches (35.6 cm) wide at the top. The origin al material is 60 inches (152.4 cm) long and 54 inches (137.2 cm) wide, allowing 2 inches (5.1 cm) extra per side which is folded outward and sewed down along the entire length. This leaves space for the supporting rods (Fig. 1e) from which the bag is susp ended. Both ends are completely lined with plastic on the inside, and a strip of plastic 5 inches (12.7 cm) wide and 15 inches (38.1 cm)long is sewed vertically to the bag adjacent to the ends beginning at the top of the bag. It is important that all seams be turned to the outside so that bats cannot climb out. An additional plastic flap 18 inches (45.7 cm) wide and 60 inches (152.4 cm) long is sewed along the edge, to the outside of the bag, 2 inches (5.1 cm) below the top on both sides of the bag. Then ea ch flap is sewed again along the length of the inside of the bag 6 inches from the top, allowing a 10 inch (25.4 cm) flap to hang free on each side. Bats are unable to climb the plastic and take shelter beneath the flaps. Metal grommets should be attached along the bottom of the bag, in the middle, and at both ends to act as drains in case of rain. A bag support plate (Fig. le) is bolted to each end of the trap 4 1/2 inches (11.4 cm) above the base. Each plate consists of a single piece of aluminum 14 inch es (35.6 cm) long, 1/8 inch (.32 cm) thick, and 116 inches (3.8 cm) wide. Five vertical slots are cut 5/8 inch (1.59 cm) deep by 1/4 inch (.64 cm) wide, at 1/2 inch (1.27 cm) intervals, beginning 1/2 inch (1.27 cm) from the end of each plate (Fig. le). Hor izontal slots 2 inches (5.1 cm) long by 1/4 inch (.64 cm) wide begin 4 inches (101 cm) from each end (Fig. le). The latter allow for adjustment of distance between the frames. The bag is hung from the support plates by means of two 72 inch (182.9 cm) alumi num rods, 1/2 inch (1.27 cm) wide by 1/4 inch (.64 cm) thick. The following nuts, bolts, and washers are required in order to assemble the trap (all are 1/4 inch (.64 cm) in diameter): 36 wing nuts, 44 regular nuts, 28 washers; (to support attachments to a ngled aluminum), 14 3 inch (7.62 cm) bolts, 10 1 1/2 inch (3.8 cm) bolts, four 2 inch (5.1 cm) bolts, and eight thumb nuts. At least 12 of the nuts must be aluminum in order to permit heliarc welding for attachment to legs. In order to string the trap wit h wire, the wing nuts on the four 5 inch (12.7 cm) threaded rods at the top of the trap (Fig. 1b) are loosened until each rod projects 3 inches below the frame. Springs are attached at 1 inch intervals along the top (Fig. lb), and the trap is strung with . 008 inch (.20 mm) diameter stainless spring steel wire. Each strand is tied individually starting at one side and working to the other. Strands should be pulled until barely tight in order to insure uniformity of tension. When the trap is strung the wing n uts at the top can be tightened slightly in order to adjust for any bow in the

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 143 middle of the frame. Capture success for bats encountering such a trap is largely dependent upon two adjustments. Of greatest importance is the tension of the vertical wires. G enerally, the wires should be tightened until no slack remains, but little or no more. Special conditions, however, necessitate occasional adjustment, depending on the speed and angle of approach of the bats. The tautness of the wires should be directly pr oportional to the speed of the bat. When bats escape by bouncing off, the wires should be loosened, and when they pass completely through both frames, tightened. The spacing of wires between the two frames is normally 3 inches. When the distance between th e frames is either increased or decreased the number of bats capable of passing through both seems to increase. It is possible, however, that slight adjustment in width effectiveness for a particular species or body size of bat. likely to pass; traps are effective in cave entrances, over trails and streams, under small bridges, under trees in open fields, and at water holes and feeding sites. Because one trap cov ers sites along a suspected flyway are usually selected, or else brush or netting is used to reduce the area through which bats may fly. I thank Mr. Arthur M. Greenhall for his initial suggestions, Dr. Ch arles O. Handley, Jr., for use of facilities at the United States National Museum, Dr. Thomas H. Kunz for his extensive testing of early trap designs, and Dr. Robert S. Hoffmann for critically reading the manuscript. This work was supported by grants from the U.S. Army Medical Research and Development Command (Contract DA 49 193 MD 2788), The University of Kansas Biomedical Sciences Support, the Theodore Roosevelt Memorial Committee of the American Museum of Natural History, and the Elizabeth M. Watkins Fun d of the University of Kansas Museum of Natural History. Literature Cited Constantine, D. C. 1958. An automatic bat collecting device. J. Wildlife Mgmt., 22: 17 22. -1962. Methodos de lucha contra los vampiros transmisores de la rabia. Bol. Ofic. Sanita ria, Panamericana, 53:7 12. -1969. Trampa portatil para varnpiros usada en programas de campana, antirrabica. Bol. Ofic. Sanitaria, Panamericana, 67:39 42. Greenhall, A. M., and J. L. Paradiso. 1968. Bats and bat banding. Resource Publ. Bur. Sport Fisheri es and Wildlife, 72:iv + 1 48. Submitted 8 Ma y 1973. Accepted 6 November 197

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 144 A Comparison of Mist Nets and Two Designs of Harp Traps for Capturing Bats by Charles M. Francis J. Mamm ., 70(4):865 870, 1989. Two widely used methods for capturing bats awa y from their roosts are mist nets and harp traps (Kunz and Kurta, 1988; Tuttle, 1974). In Australia, Tidemann and Woodside (1978) found that harp traps were about 10 times more effective than mist nets at catching small to medium sized vespertilionids and rhinolophids. In Costa Rica, LaVal and Fitch (1977) found that traps were about 1.7 times as effective as nets. However, there is some evidence of variation among species in their susceptibility to traps. LaVal and Fitch (1977) reported that large phyllost omids frequently were caught in mist nets and rarely were trapped, whereas the reverse was true for several small vespertilionids. Such interspecific variation in susceptibility can affect the choice of capture methods for a particular study, and must be c onsidered in community studies if the number of captures is used as an index of relative abundance of species (Fleming, 1986). In this paper, I compare the effectiveness and selectivity of mist nets and harp traps in the understory of Malaysian rain fores t. I also compare the relative success of two different designs of harp traps. The original harp traps had a single bank (row) of wires and were effective for capturing fast flying bats such as molossids, but not for more maneuverable species (Constantine, 1958). Subsequently, traps with two banks of lines were used widely (Tidemann and Woodside, 1978; Tuttle, 1974), but even these may capture less than half the bats encountering them (Kunz and Anthony, 1977). I developed new designs of harp traps with addi tional banks of lines, and present here data on the trapping efficiency of four bank traps compared with two bank traps. The study was conducted between 1981 and 1987 in two areas of lowland rain forest in Malaysia: Pasoh Forest Reserve in Peninsular Mala ysia (2 58'N, 102 17'E), and Sepilok Forest Reserve in Sabah, northern Borneo (5 52'N, 117 56'E). The forest in both areas was unlogged and dominated by trees of the family Dipterocarpaceae. The canopy was 30 60 m tall, and blocked much of the light except where treefalls had created gaps. All trapping and netting was done in the understory < 2 m above the ground along a network of trails. Harp traps were built from modifications of the design of Tidemann and Woodside (1978). The original design included c ollapsible horizontal and vertical poles for the

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 145 frame, but I used single poles to increase rigidity and to simplify construction. The first trap was built with wooden poles and metal joints, but was unsatisfactory because it lacked stability. The remainin g traps were built with aluminum frames (Fig. 1). The corners were welded to the horizontal poles in some traps and were detachable in others. The traps were portable, as they could be dismantled into a bundle about 160 cm long and 15 cm in diameter, and w eighing 6 8kg. Dismantling or assembly of the traps took 5 10 min. Some traps were modified to accommodate as many as four banks of lines by widening the crossbars and the bag (Fig. 1). All traps were strung with 0.20 mm diameter (2.7 kg test) nylon fishin g line, tied just barely taut. When the traps were set, tension was applied by lengthening the vertical poles of the frame 10 15 cm (7 10% of total length). Lines were spaced 2.5 cm apart within each bank, and banks were 7.5 cm apart. Line spacing on adjac ent banks was offset by 1.25 cm for two and three bank traps. On four bank traps the middle two banks were aligned with each other, but offset from the outer banks. Traps usually were placed across well established trails or small stream beds, and were m oved at 1 4 day intervals. They were set all night and inspected one or more times in the evening, then again shortly after dawn. Occasionally, I watched them for short periods at dusk. One to three traps were set each night, for a total of 126 trap nights at Sepilok (two bank and three bank traps), and 53 trap nights at Pasoh (40 nights with two bank traps, 13 nights with four bank traps). Captures in the three bank trap were not distinguished consistently from those in the two bank traps, so I could not e valuate relative efficiencies of different designs of traps at Sepilok. More than 98% of mist netting was done with 12 by 2 m nets with 36 mm mesh, although occasionally one or two 6 by 2 m nets also were used. Nets were set at approximately 50 m interv als along a grid of trails, and were open continuously for 2 5 days. They were inspected once or twice in the early evening and again at dawn for bats, then at 2 h intervals through the day for birds. On a few nights I watched single nets continuously for about an hour at dusk. An average of 25 nets was set simultaneously, and operated for 27 nights at Pasoh (675 net nights) and 39 nights at Sepilok (975 net nights). Trapping coincided with netting on most nights at Pasoh, but at Sepilok traps were set on many nights in addition to those when nets were set. Captured bats were weighed to 0.1 g with a Pesola spring balance to determine the average mass of each species. Species identifications follow Payne and Francis (1985), except for species found only in Peninsular Malaysia which follow Medway (1978). Analyses initially were performed separately for the two sites, but because the results were essentially the same in both areas, only combined data are presented here. During the study, I caught 798 bats in traps (4.46/trap night) and only 222 in nets (0.135/net night). The greater efficiency of traps is particularly notable considering they had only about 12% of the surface area of nets (3 m2 for traps compared with 24 m2 for most of the nets). Expressed by area, nightly captures in traps averaged 1.49 bats/m2 compared with only 0.0057 bats/m2 in nets. However, if bats tended to follow trails, such a comparison may not be justified because the area of each net over a trail was similar to that of each trap. N ets and traps were examined only a few times each night, so some bats may have escaped between inspections. Most mornings I found holes in nets made by bats that were caught but escaped. I also saw a few bats escape from the top of the trap bags, so the ca pture rate for both nets and traps would have been greater had they been watched continuously. Megachiropterans were captured at similar rates in traps and nets, but microchiropterans were captured nearly 60 times more frequently in traps (Table 1). The l ow rate of capture of Microchiroptera in nets was probably related to their abilities to escape from nets and to detect nets with echolocation, thus avoid them. Most Microchiroptera caught in nets had chewed part of the net around them, and some were seen to escape before I could secure them. In contrast, Megachiroptera caused relatively little damage to nets, thus, were unlikely to have escaped often. When observing nets and traps at dusk, I noted that most Microchiroptera encountering nets avoided hitting them, whereas those encountering traps generally were captured or flew through the lines. I did not observe Megachiroptera encounter nets or traps, but they would be unlikely to detect and avoid either because none of the species captured in this study is known to echolocate. For both suborders of bats, species of large body size generally were more susceptible to capture in nets (Table 1). In mist nets, both the medium sized Cynopterus brachyotis (mean body mass = 26g) and the smaller Balionycteris macul ata (13g) were caught commonly (47

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 146 Table 1 . Comparison of the number of captures of bats in mist nets and harp traps, by suborder, and within each suborder and major family of Microchiroptera, by species grouped into size classes. Combined data from Pasoh and Sepilok in Malaysia. Category Mist nets Mist nets Harp traps Harp traps Mass a (g) n Rate (bat/100 net nights) n Rate (bat/100 net nights) P b Suborders: Megachiro ptera 98 5.9 10 5.6 <0.001 Microchiroptera 124 7.5 788 440.2 Species w/in suborder: Megachiroptera 10 20 48 2.9 9 5.0 <0.01 20 80 50 3.0 1 0.6 Microchiroptera 3 5 1 0.1 127 70.9 <0.001 5 10 38 2.3 526 293.9 10 20 68 4.1 124 69.3 20 6 0 17 1.0 11 6.1 Species within family: Hipposideridae 5 10 11 0.7 341 190.5 <0.001 10 20 5 0.3 50 27.9 20 50 12 0.7 11 6.1 Rhinolophidae 5 10 8 0.5 22 12.3 0.04 10 20 56 3.4 63 35.2 Vespertilionidae 3 5 1 0.1 128 71.5 <0.001 5 10 15 0. 9 161 89.9 10 20 1 0.1 11 6.1 a Bats were assigned to size categories based on the mean body mass of the species b log likelihood ratio test (G test) whether captures were independent of trap type. For Hipposideridae and Vespertilionidae, the two la rgest size categories were combined because of small sample sizes and 43 captures, respectively). One to three individuals each of six other species, ranging in size from 14 to 75g, also were netted. In harp traps, nine of 10 fruit bats captured were B. maculata ; only one C. brachyotis was caught. Many microchiropteran species were captured in traps and nets, but most individuals of smaller species were taken in traps. The trend for larger species to be captured relatively more frequently in mist nets also held for each of the three fam ilies of Microchiroptera with more than two species in the sample (Table 1). Additionally, there were differences among families of Microchiroptera in trapping rate independent of body size. The small and medium sized Rhinolophidae were netted more frequen tly than similarly sized Hipposideridae (Table 1). Four of five Emballonura alecto (6.4g) and E. monticola (5.4g) were captured in nets despite their small size. All five Megaderma spasma (25.6g) and all six Nycteris javanica (15.6g) were netted despite th e frequent capture of larger species of Hipposideros in traps. Some of the interspecific differences in capture frequency of Microchiroptera could be related to variation in the structure of their echolocation calls. Call structure for most Malaysian bat s has not been described, but data are available on the constant frequency components of calls of four species of Rhinolophus and six of Hipposideros from peninsular Malaysia (Feng and Tyrell, in press; Heller, 1985). I compared these frequencies with the number of captures of each of these 10 species. In general, species with high frequency calls were small and rarely were caught in nets. However, small species (< 10g) with lower frequency calls ( H. ridleyi , 61 kHz; R. sedulus , 64 kHz; R. refulgens , 98 kHz ) were netted relatively more often than similarly sized species with high frequency calls ( H. sabanus , 200 kHz; H. cervinus , 126 142 kHz; H. bicolor , 141 kHz). The ratio of captures in traps to captures in nets was 23:7 for low frequencies and 296:9 for h test, P < 0.001). The larger species (> 12g) had lower frequency calls (< 76 kHz), and were netted even more often than smaller species with calls of similar frequency. The ratio of captures in traps to captures in nets was 73:68 for large bats and 14:4 for the two small species with the suggests that both call frequency and body size influence capture rate in nets. The relatively high rate of capture of Rhinolophus in nets, compared to Hipposideros , may be

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 147 related to the generally lower frequency calls of the former. Data from Pasoh Forest Reserve were used to compare four bank traps with two bank traps. Overall, two bank traps caught 170 bats in 40 trap nights (4.3 ba ts/trap night), whereas four bank traps caught 110 bats in 13 trap nights (8.5 bats/ trap night). However, these totals include records of two bank traps from several different trapping sessions, whereas the four bank traps were used only in late August 19 87. During the latter session, a two bank trap, set in approximately the same locations as the four bank traps although on different nights, caught only 12 bats in eight trap nights (1.5 bats/trap night). Thus, it appears that four bank traps were 2 6 time s more efficient than two bank traps. However, further data are required to confirm the difference statistically because of high variation in nightly trapping success. There were significant differences in the effectiveness of the two types of traps for d ifferent species of bats. Capture rates for 5 10 g bats were similar in both two bank and four bank traps (2.5 and 3.0 bats/ trap night, respectively; 101 and 39 individuals). However, smaller bats were caught slightly more frequently in two bank traps (0. 5 and 0.2 bats/trap night; 21 and three individuals), whereas larger bats were caught much less frequently (1.1 and 5.0 bats/trap night; 45 and 65 individuals). Overall, the relative differences were highly significant (G = 34.0, P < 0.0001). Personal obs ervations on a few nights indicated that fewer bats flew straight through four bank traps than two bank traps. Because of darkness, I could not determine the position of the wings when bats hit the traps, but those bats flying through the lines invariably hit them with sufficient force to make a clearly especially larger species, have sufficient momentum to force their way between two banks of line, but insufficient to fly through four. However, despite the imp roved efficiency, some bats still can fly through the four bank traps. The observed differences between traps and nets in capturing Malaysian bats support previous studies showing harp traps to be more effective than mist nets (Laval and Fitch, 1977; Tide mann and Woodside, 1978). This study also confirms the existence of interspecific variation in relative susceptibility to traps or nets (Laval and Fitch, 1977). For studying community structure, an ideal trapping method produces captures of bats in proport ion to the abundance of each species in the community. Other sampling methods can be used, however, provided that the extent of their biases can be estimated. It was not possible from this study to determine the exact biases because the actual number of ea ch species in the forest was not known. The greater ability of some bats to escape from mist nets is a factor that influences number of captures. All Megachiroptera are frugivorous or nectarivorous; their teeth have rounded or pointed crowns that did not appear to be effective at cutting nets. Frugivorous phyllostomids also have reduced dentition and frequently are captured in nets (Laval and Fitch, 1977), suggesting that they similarly may be inefficient at chewing nets. In contrast, all Microchiroptera c aught in this study were insectivorous; their teeth have sharp cutting edges with which they readily chewed holes in nets to enable escape. Body size also is related to trapping success. The greater momentum of large bats apparently increased their abilit y to fly straight through harp traps, at least those with two banks. This suggests that large bats were under sampled by two bank traps. In addition, large bats generally have higher wing loadings and cannot turn as sharply (Aldridge, 1987). This could hav e resulted in over sampling of large bats by mist nets if the bats were less able to avoid nets. Interspecific variation in echolocation calls also appears to influence capture rates in nets. Megachiroptera, of which none of the species in this study are known to echolocate, were caught frequently in mist nets. They rely entirely on vision for navigation, and it is unlikely, in the darkness of the forest understory, that they could detect either mist nets or traps before hitting them. In contrast, all spec ies of Microchiroptera probably are capable of detecting mist nets by echolocation, although with different degrees of resolution. Species with high frequency calls seemed to be least susceptible to mist nets, possibly because these frequencies better reso lve small targets such as knots in mist nets (Feng and Tyrell, in press). Alternatively, bats with high frequency calls may be adapted for short distance maneuvering, because their calls attenuate more rapidly and probably have a shorter range (Novice, 197 7). Variation in echolocation calls also may have influenced captures in traps. Most bat species examined in the laboratory can echolocate vertical wires < 0.2 mm in diameter even at much greater spacing than the lines on traps (Novick, 1977). Kunz and Ant hony (1977) noted that

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 148 placed near their roost. However, those bats may have used vision, because the observations were conducted at dusk in relatively open areas. Further data are required to determine whether bats that hit traps fail to detect them, or detect them and attempt to fly through them. Other factors that can affect capture rates of bats include microhabitat and height at which the trapping device is set, opportunities for bats to avoid the d evice, proximity to food or water supplies, ambient weather and light conditions, age and experience of the bats, and behavior (e.g., commuting or foraging) of the bats (Constantine, 1958; Kunz and Anthony, 1977; Kunz and Kurta, 1988). Insofar as the effec ts of these factors vary among species, the proportion of species in the sample will be biased. It is unlikely that any capture method will produce a completely unbiased sample. Factors other than biases also may influence the choice of capture methods fo r a particular study. Of methods tested in this study, four bank traps were the most effective, at least for Microchiroptera, and were probably least biased. However, they are slightly more expensive, more time consuming to build and set, and weigh slightl y more than two bank traps. Further experiments with different spacing, sizes, or tensions of lines may show that other designs of traps are even more effective. Also, for some groups of bats such as Megachiroptera, mist nets apparently were as effective a s traps. Given their low cost and portability, mist nets still may be preferable for some studies, even of Microchiroptera, especially if they are watched closely to minimize escapes (Kunz and Kurta, 1988). However, the potential biases must be considered during analysis. Simple capture rates with any method should be used as an index of relative abundance with caution. This study was conducted incidental to research on forest bird populations funded by the Canadian development agency CUSO, the Wildlife Se ction of the Sabah Forest Department, and the Natural Sciences and Engineering Research Council of Canada. The socioeconomic planning unit of the granted permission to conduct wildlife research in Malaysia. The Forest Research Institute of Malaysia gave permission for research in Pasoh Forest Reserve. The Sabah Forest Department funded construction of two bat traps and supplied some mist nets. D.R. Wells and the University of Malaya assisted with construction of three more traps and supplied nets for use at Pasoh. D.G. Constantine, M.B. Fenton, T.H. Kunz, and E.D. Pierson helped to improve the manuscript with their comments. Literature Cited Aldridge, H. D. J. N. 1987. Turning flight of bats. J. Exp. Biol., 128:4 19 425. Constantine, D. G. 1958. An automatic bat collecting device. J. Wildl. Mgmt., 22:17 22. Feng, A. S., and K. Tyrell. In press. Do signal characteristics determine a bat's ability to avoid obstacles? In Animal sonar systems, Vol. 3 (P. Nachtigall, ed .). Plenum Press, New York. Fleming, T. H. 1986. The structure of Neotropical bat communities: a preliminary analysis. Rev. Chilena Hist. Nat., 59:135 150. Heller, K.G. 1985. The echolocation calls of 12 syntopic rhinolophid species (Rhinolophus, Hipposide ros). Bat Res. News, 26:61. Kunz, T. H., and E. L. P. Anthony. 1977. On the efficiency of the Tuttle bat trap. J. Mamm., 58: 309 315. Kunz, T. H., and A. Kurta. 1988. Capture methods and holding devices. Pp. 1 29, in Ecological behavioral methods for the s tudy of bats (T. H. Kunz, ed.). Smithsonian Institution Press, Washington, D.C., 533 pp. LaVal, R. K., and H. S. Fitch. 1977. Structure, movements and reproduction in three Costa Rican bat communities. Occas. Papers Mus. Nat. Hist., Univ. Kansas, 69:1 28. Medway, L. 1978. The wild mammals of Malaya (Peninsular Malaysia) and Singapore. Oxford Univ. Press, Kuala Lampur, 128 pp. Novick, A. 1977. Acoustic orientation. Pp. 73 287, in The biology of bats (W. A. Wimsatt, ed.). Academic Press, New York, 3:1 651. Pa yne, J., and C. M. Francis. 1985. A field guide to the mammals of Borneo. Sabah Soc., Kota Kinabalu, 332 pp. Tidemann, C. R., and D. P. Woodside. 1978. A collapsible bat trap and a comparison of results obtained with the trap and with mist nets. Australian Wildl. Res., 5:355 362. Tuttle, M. D. 1974. An improved trap for bats. J. Mamm., 55 475 477. Submitted 13 July 1988. Accepted 13 January 1989.

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 149 Comparison of Sampling Methods for Inventory of Bat Communities Carles Flaquer,* Ignacio Torre, and Antoni Arrizabalaga Museu de Granollers Cienc ies Naturals, 51 Francesc Macià , E 08402 Granollers, Barcelona, Spain Journal of Mammalogy, 88(2):526 533, 2007 * Correspondent: From 1999 to 2005, we sampled the bat fauna of Catalon ia (northeastern Spain, Mediterranean region) using 3 methods (bat detectors, mist nets, and roost surveys) and determined the total number of bat species present (S = 22). Twelve bat species and 5 acoustic groups ( 5 different species) were identified usi ng bat detectors, 17 species were found during roost inspections, and 13 species were trapped using mist nets. However, mist nets yielded the highest species richness per number of individuals sampled, as demonstrated by rarefaction. Some species were alwa ys either over or under sampled according to the sampling method used. We also evaluated 3 guilds of bats defined by summer roost preferences, documenting a significant correlation between guild and detection method; cavity roosting bats were underreprese nted when only bat detectors and mist net surveys were used, whereas rock crevices or man made structure and tree guilds were underrepresented when only roosts were surveyed. Different techniques should be used to assess the richness of bat communities and we recommend combining all the methods described above in future bat surveys. Key words: bat communities, bat detectors, Mediterranean region, mist nets, roosts, sampling methods, species richness, surveys The order Chiroptera is the 2nd most diverse o rder of mammals (Wilson and Reeder 2005) and exhibits great numerical, taxonomical, functional, and ecological diversity (Simmons and Conway 2003; Stevens and Willig 2002). However, assessing the distribution of bat species and the composition of bat commu nities is a challenge (Jaberg and Guisan 2001) because their nocturnal behavior, large home ranges, and the problems associated with species identification in flight (Walsh and Harris 1996) make accurate surveys difficult. Studies of bat distribution and habitat preferences use different sampling techniques to describe the great complexity of bat communities. From the analysis of specimens housed in museum collections (L ó pez Gonz á lez 2004) to the use of advanced technology (i.e., bat detectors Vaughan et a l. 1997), numerous different methods of sampling bats are currently in use, although today most researchers employ a combination of techniques (Duffy et al. 2000; Jaberg and Guisan 2001). Bat detectors enable bats to be studied in greater detail and are n ow employed by most researchers in censuses of bat faunas (Barataud 1998; Ciechanowski 2002; Pauza and Pauziene 1998) and in the analysis of habitat use (Avila Flores and Fenton 2005; Vaughan et al. 1997; Wickramasinghe et al. 2004). Despite their shortcom ings (Hayes 2000), bat detectors frequently are used in annual monitoring programs (Walsh et al. 2001). However, scientists have become concerned with the validity of data derived from this method. Over the last decade a growing number of studies have exam ined the advantages and disadvantages of techniques using bat detectors (Ahl é n and Baagoe 1999; Barclay 1999; Hayes 2000) and various authors have analyzed sampling methods for bats in a search for better bat survey strategies (Duffy et al. 2000; Murray et al. 1999; acoustic sampling methods seem to yield greater species and Gannon 1999), almost all authors agree that echolocation monitoring should be but one component of bat surveys and that a combination of techniques is required for more comprehensive inventories (Barclay Mist nets have several drawbacks: they are time consuming to set up, need to be placed in flyways or water sources with good canopy coverage over the net, cause stress in animals, and, moreover, obtain biased samples of bat species assemblages (Murray et al. 1999). Harp traps are less stressful; however, the species sampled varies with body size, fligh t patterns, and type of echolocation (Duffy et al. 2000). On the other hand, bat detectors cause no stress to bats, although the data they produce also are biased, because high flying bats and those that emit low intensity calls are underrepresented (Barcl ay 1999; Duffy et al. 2000).

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 150 Other techniques should be considered in bat survey studies. Finding roosts in man made structures or in caves and mines represents a useful survey method; several bat species can be inventoried in roosts or when they leave ro osts at sunset (Mitchell Jones and McLeish 1999; Tuttle et al. 2000). Another technique that should be considered is bat box surveys. These artificial roost sites should not be viewed merely as alternative roosts sites (Brittingham and Williams 2000; Flaqu er et al. 2006; Lourenço and Palmeirim 2004) and are useful for providing data on bat communities, especially in areas with a lack of old trees bearing natural roosting sites (Flaquer et al. 2007). Bat boxes may be particularly effective for surveying bats in woodland habitats; for example, at least 73% of British bats are known to have roosted in boxes (Mitchell Jones and McLeish 1999; Stebbings and Walsh 1991). Because of their peculiar climatic and ecological features, Mediterranean countries differ rem arkably from the areas of Europe where most data on habitat use by bats have been gathered. Yet, little is known about habitat preference in bats in the Mediterranean Region (Russo and Jones 2003). From 1999 to 2005, we studied the bat fauna in and around 10 natural areas distributed along the Catalan Mediterranean coastline in northeastern Spain. Captures of bats with mist nets and roost surveillance were combined with the use of ultrasonic detectors. We discuss the advantages and disadvantages of each met hod and compare the efficiency of each technique for assessing species richness of bats. Additionally, we provide recommendations for future monitoring and survey strategies in this region. M ATERIALS AND M ETHODS Study area . The Catalan coast is located in the northeastern Iberian Peninsula (40 ° 42 N, 0 ° 50 E) and comprises 580 km of coastline and littoral and pre littoral mountain ranges covering 31,000 km 2 and ranging from sea level to 1,700 m in elevation. The predominant climate is Mediterranean (annual m ean temperatures around 15 ° C and annual precipitation between 500 and 700 mm/year). Climate varies with topography, although summers generally are dry and hot (precipitation , < 200 mm/year and mean temperatures around 20 ° C), whereas spring and autumn are w et. Vegetative communities are dominated by Quercetum ilicis galloprovinciale and Quercus mediterraneo montanum , although scattered beech ( Fagus sylvatica ) forest could be found in the coldest areas. Identification of bats . Bats were identified in the fie ld based on morphological and dental criteria in live bats (Arthur and Lemaire 1999; De Paz and Benzal 1990; Helversen 1989; Menu and Popelard 1987; Palmeirim 1990; Schober and Grimmberger 1996). Additionally, we used ultrasonic bat detectors (models D230 and D240x; Pettersson Elektronics AB, Uppsala, Sweden) with frequency division, heterodyne, and time expansion ( x 10) systems, as well as a portable digital tape (SONY TCD D8; Sony Corporation, Tokyo, Japan) and a laptop computer to record echolocation and social calls ( Ahl é n 1990; Barataud 1996; Russ 1999). Sounds were analyzed by Bat Sound (Pettersson Elektronics AB). We used a sample frequency of 44,100 samples/s, 16 bits/sample, and automatic fast Fourier transform (a mathematical formula for calculating frequency data from time data) with a Hanning window (Russ 1999). Recordings were screened for the presence of the characteristic social calls emitted during the mating period (Russ 1999; Russo and Jones 1999) and calls were identified by means of a libra ry of known echolocation call sequences for each species. Identification of the soprano pipistrelle ( Pipistrellus pygmaeus Miniopterus schreibersii ) were based on presence of social calls, observations of wing shape in good condition s, or both ( Ahl é n 1990). For the purposes of acoustic identification, we treated the following pairs of species eared bats ( Myotis blythii/M. myotis ( Myotis nattereri/M. emarginatus ), Da fingered bats ( Myotis daubentonii/M. capaccinii ), noctule/greater noctule ( Nyctalus noctula/N. lasiopterus ), and brown/gray long eared bats ( Plecotus auritus/P. austriacus Ahl é n 1990; Ahl é n and Baagoe 1999; Barataud 1996). Bat survey techn iques . Between 1999 and 2005, we randomly used 3 different approaches for sampling bat species richness of bats (bat detectors, mist nets, and inspection of roosts), from April to November, in 10 natural areas located along the Catalan coast. In all, we s urveyed 418 independent bat detector stations at heights from sea lev el to 1,629 m above sea level ( X = 359 m ± 417 SD ). We used D240x and D230 bat detectors and activity was quantified by counting the number of passes per 10 min at each point (Wickramasin ghe et al. 2003). The D230 detector was tuned to use frequency division, which provides for both broadband (records all frequencies) and continuous

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 151 (records all bat passes) recording. We recorded the output from frequency division on channel 1 of the porta ble digital recorder and we used the time expanded output from detector D240x to record bat calls from each pass on channel 2 of the portable recorder (Vaughan et al. 1997). According to Ahlé n and Baagoe (1999), time expansion sounds retain call structure and have high sound quality and so can be analyzed to identify species. Additionally, we used the heterodyne system from the detector D240x scanned up and down to cover all frequencies (Ahl é n and Baagoe 1999). We used standard techniques to mist net bats and Gannon 1999). Net heights varied from 2.5 to 3 m and lengths varied from 3 to 18 m and were placed along or around waterways, ponds, and flyways. The amount of time employed and the number of nets used depended on the physical characteristic s of each location independent stations with mist nets representing 3,561 m 2 of mist net collecting surface operating for a total of 175.4 h. These stations were situated at elevations between 4 1 and 1 ,481 m above sea level ( X = 643 ± 373 m). We operated mist nets for 173.8 ± 82.7 min (range 60 590 min) and had a mean length of 17.1 ± 8.1 m (range 3 35 m). We used standard techniques to find roosts (mines, caves, and man made structures Mitchell Jones and McLeish 1999; Tuttle et al. 2000), and we applied guidelines established by Mitchell Jones and McLeish (1999) to identify and count bats in roosts. The 271 roosts found and visited were situated at elevations from sea lev el to 1,300 m above sea level ( X = 346 ± 312 m) and were visited 2.0 ± 3.1 times (range 1 28; total visits 541). Roosts sampled more than once were visited in Statistical analysis . We used 3 statistical approaches to identify and quantify possible sampling biases between the 3 different methodologies employed in the study. First, we used a log linear analysis to search for differences between the 3 sampling methods in the species composition and abundance of bat communities (Torre et al. 2004). This technique allowed us to determine what species were under or oversampled by each sampling method. The standardized residuals after the log linear analysis were used to represent the degree of deviance from the null model (no under or o versampling of a species by a sampling method), and the statistical significance was verified by examining the components of maximum likelihood comparing these values with the critical level of significance ( 2 = 3.84, d.f. = 1, P < 0.05). Second, we used the nonparametric Kruskal Wallis test (Zar 1996) for comparing methods, because species richness and abundance did not have a normal distribution within the sampling methods and had a heterogeneity of variances. Because no post hoc tests are available for nonparametric tests, we conducted pairwise comparisons and used Bonferroni corrections to correct for significance level (Rice 1989); thus, our acceptable critical region was P = 0.05/ 3 = 0.0166. Finally, given that the total number of individuals observe d varied among methods, we used rarefaction to provide a meaningful interpretation of the different species richness found in each of the 3 sampling methods. Rarefaction takes into account species richness and abundance and allows comparisons between assem blages of equivalent numbers of individuals. We used Ecosim 7.0 software (N. J. Gotelli and G. L. Entsminger 2001, Ecosim: null models software for ecology, to generate individual based rarefaction curves of species richness and associated variance for each of the 3 sampling methods (Lambert et al. 2005; Torre et al. 2004). The computer sampling algorithm of the program randomly draws a sample of specified size from the total sample and computes a mean and a v ariance for species richness after 1,000 iterations. The individual based data sets were obtained after pooling replicated samples into single ones for each sampling method (Gotelli and Colwell 2001). The statistical comparison of species richness by rare faction curves and of the number of individuals depends on the correct assessment of the number of individuals captured, counted, detected, or a combination of these. Roost surveys and mist netting both allow determination of the number of individuals coun ted or trapped for every species sampled, despite that the number of individuals sampled represent a fraction of the population. Bat detectors, on the other hand, count bat passes but cannot identify individuals. The number of passes detected likely is cor related to the number of individuals (Wickramasinghe et al. 2003), although there is no way of enumerating exactly the number of individuals present on the basis of passes counted because bat detector samples may count the same individual more than once. T his will have a negative effect on estimates of species richness carried out by rarefaction (i.e., species richness will be underestimated).

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 152 All methods and procedures used in the present study followed the guidelines for the capture, handling, and care of mammals as approved by the American Society of Mammalogists (Animal Care and Use Committee 1998). R ESULTS In all, the 3 sampling methods detected 22 species of bats in the study area and revealed qualitative and quantitative differences between bat com munities according to the sampling method. Twelve bat species and 5 acoustic groups ( 5 different species) were identified using bat detectors, 17 species were found during roost inspections, and 13 species were trapped using mist nets (Table 1). Some species were identified [ Pipistr ellus nathusii] , M. nattereri , and M. capaccinii ; mist nets: Plecotus auritus ; bat detectors: European free tailed bat [ Tadarida teniotis ]), although some of these species form part of acoustic pairs. A log linear analysis was performed with frequencies o f occurrence for all the identified species (22) and for each sampling method, yielding highly significant differences (interaction of species x method: G = 12,842, d.f. = 42, P < 0.0001). All the species sampled except M. capaccinii and P. nathusii showed significant differences between the 3 sampling methods in their frequencies of occurrence. Members of the family Rhinolophidae and M. myotis, M. nattereri, M. emarginatus , and M. schreibersii were oversampled by roost inspections, but under sampled by bat detectors (Fig. 1A). On the other hand, P. auritus, P. austriacus, M. daubentonii , common pipistrelle ( P. pipistrellus ), P. kuhlii Hypsugo savii ), serotine ( Eptesicus serotinus ), western barbastelle ( Barbastella b arbastellus ( Nyctalus leisleri ) were oversampled by the use of bat detectors and mist nets, but under sampled by roost inspections (Fig. 1B). P. pygmaeus was oversampled by bat detectors and under sampled by roost inspections and ne ts, T. teniotis was oversampled by bat detectors and under sampled by roost inspections, and M. blythii was oversampled by net sampling. Some species, such as P. pygmaeus and P. pipistrellus , were detected mainly by bat detectors (40.8% and 13.6%, respecti vely), whereas others were most often detected by roost inspections, such as M. schreibersii and R. ferrumequinum (51.4% and 7.8%, respectively), or by mist netting, such as H. savii and P. austriacus (20.5% and 13.4%, respectively; Table 1). A 2nd log li near analysis was performed by grouping bat species into 3 guilds on the basis of their summer roost preferences: cavities ( Rhinolophus sp., M. myotis, M. blythii, M. nattereri, M. capaccinii, M. emarginatus, P. austriacus, P. auritus , and M. schreibersii ) , trees ( Nyctalus, P. nathusii , and B. barbastellus ), and rock or man made structure crevices ( P. pipistrellus, P. pygmaeus, M. daubentonii, P. kuhlii, H. savii, E. serotinus , and T. teniotis ). Once again, differences in frequencies of occurrence between s ampling methods for the 3 guilds were highly significant (interaction of guild x method: G = 9,679, d.f. = 4, P < 0.0001) and were found for the 3 paired comparisons. As can be seen in Fig. 2, roost inspections oversampled cavity dwelling species, but unde r sampled both the crevice and tree roosting guilds. Bat detectors oversampled the crevice roosting guild and, to a lesser extent, the tree roosting guild, whereas they under sampled the cavity roosting guild. Finally, mist nets oversampled the crevice a nd tree roosting guilds, but under sampled the cavity roosting guild. We observed a high degree of agreement in species occurrence frequencies for bat detectors and mist netting and, in most cases, both methods over or under sampled estimates for the same species. A log linear analysis performed using the frequencies of occurrence from stations with 0 9 species detected by all sampling methods yielded highly significant differences (interaction of species richness x method: G = 47.45, d.f. = 18, P < 0.000 1). Mist nets and roost surveys showed a higher proportion of sampling stations with negative records (50% and 46% with no species recorded, respectively), whereas bat detectors showed a higher proportion of sampling stations with 2 and 3 species (23% and 10% of the total stations, respectively; Fig. 3). Frequencies of occurrence of 1, 4, 5, 6, and 9 species per station did not differ between sampling methods (Fig. 3). The number of individuals sampled differed greatly between methods, with a total of 13,4 77 individuals counted in roost inspections, 6,031 bat passes (contacts) counted with bat detectors, and only 128 bats captured in mist nets. The mean number of species detected per station by bat detectors was 1.33 ± 1.22 ( SD ), with a range of 0 6 species . The mean number of contacts per station was 14 ± 25 ( SD ), with a range of 0 186. The mean number of species detected by roost surveys was 0.81 ± 0.96 ( SD ), with a range of 0 5 species. The mean number of bats per roost was 49.7 ± 320 ( SD ), with a range o f 0 5,000. The mean number of species detected

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 153 by mist netting was 1.01 ± 1.54 ( SD ), with a range of 0 9 species. The mean number of bats captured per station was 2.0 ± 4.3 ( SD ), with a range of 0 30. The species richness detected was significantly higher for bat detectors than for mist net stations ( H = 8.24, d.f. = 1, P = 0.004) or for roosts ( H = 33.55, d.f. = 1 , P < 0.0001), although no significant difference was detected between mist nets and roosts ( H = 0.01, d.f. = 1, P = 0.89). The number of indiv iduals or contacts per station was higher for bat detectors than for mist nets ( H = 43.96, d.f. = 1, P < 0.0001) or for roosts ( H = 36.85, d.f. = 1, P < 0.0001), although no significant difference was detected between mist nets and roosts ( H = 3.25, d.f. = 1, P = 0.07). However, because species richness increases with the number of individuals recorded, we generated individual based rarefaction curves to compare species richness between sampling methods for the same number of individuals. Mist nets had the highest richness per number of individuals sampled, followed by bat detectors and then roost surveys (Fig. 4). D ISCUSSION The combination of sampling methods used in our Mediterranean study area during the 6 years of sampling detected 22 species of bats. This number agrees with the total number of bat species known to be present in the area (Flaquer et al. 2004; Palomo and Gisbert 2002; Serra Cobo 1987) and represents 85% of species belonging to the very rich Iberian bat fauna (Palomo and Gisbert 2002). Ov erall, 77% of the species were detected by acoustic monitoring, 77% at roost sites, and 59% with mist nets. Our results confirm that combined survey techniques are required for thorough bat as has been found for terrestrial small mammals in the same area (Torre et al. 2004). Although the sampling effort was intense, the rarest species in the study area ( P. nathusii, M. nattereri, M. capaccinii, P. auritus , and N. noctula/N. lasiopterus ) were detected b y only 1 method, a fact that indicates that rare species may be easily overlooked if only 1 inventory technique is used. On the other hand, common species such as P. pygmaeus were identified by all the (1999) and Murray et al. (1999), the number of species detected by bat detectors was significantly higher than that detected by mist nets, whereas roost inspections yielded the same species richness as bat detectors. Nevertheless, mist nets and roost surveys had a higher proportion of sampling stations with negative records and in almost half of the stations our sampling efforts were fruitless; in these localities, detectors were a more efficient method. Of all methods, mist nets detected the highest species rich ness per number of individuals sampled, probably because of biases related to the location of sampling stations near ponds or rivers, especially suitable habitats for bats in the Mediterranean region (Russo and Jones 2003). Species rich sites were found in dry regions wherever nets were located near the isolated ponds or rivers and at 1 station we detected 9 different species on a single night, the highest number of species detected by any sampling method at a single station in this study. According to ou r results, the most viable method for assessing species richness of cavity roosting bats (especially Rhinolophus ) is to find their roosts, a limitation that should be taken into account in studies where only mist nets and bat detectors are used. On the oth er hand, roost finding techniques under represent crevice and tree roosting bats. We ruled out the use of climbing as a means of examining tree roosts (Ruczy ski and Bogdanowicz 2005) because this method is highly time consuming and requires specially trained researchers. Furthermore, the Catalan forests lack old trees bearing natural roosting sites as a consequence of forest management practices that emphasiz ed timber extraction until the middle of the 20th century (Flaquer et al. 2007, and references therein). In light of the results from wetlands in the study area (Flaquer et al. 2005, 2006), it is likely that the lack of old trees in the study area with sui table roost sites will increase the importance of bat boxes (Flaquer et al. 2006; Ruczy ski and Ruczy ska 2000). Field surveys based on captures in mist nets and harp traps provide the opportunity to collect biological and morphological data that cannot be obtained with bat 1999). Furthermo re, some species are easier to capture in mist nets than with other capture methods. We believe that annual bat capture programs based on intensive small scale trapping in mist nets and harp traps (Mitchell Jones and McLeish 1999) would be a useful tool fo r sampling bat communities. Although some European research has focused on analyzing changes in bat populations (Ransome and Hutson 1999; Walsh et al. 2001), little is known about bats in the Mediterranean region (Russo and Jones

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 154 2003). We documented that a combination of capture and bat detector techniques is effective (Duffy et al. roosting bats and some rare species often are underrepresented. Without roost survey techniques we would have missed 3 of the 22 species encountered. Therefore, roost surveys are essential for assessing bat species richness in Mediterranean areas; finally, although not studied here and as an untested recommendation, we believe that the lack of old trees could make the use of bat boxes useful in bat surveys in this region. We recommend combining all the methods described above in future surveys and monitoring programs for Mediterranean bats. R ESUMEN Entre los a ñ os 1999 y 2005, la fauna de quir ó pteros de Catalu ñ a (NE Espa ñ a, regi ó n Mediterr á nea) fue inventariada usando 3 m é todos de muestreo (detectores de ultrasonidos, redes de niebla y visitas a refugios) obteniendo informaci ó n sobre las 22 especies de quir ó pteros presentes en la zona. Doce especies y 5 grupos ac ú sticos ( 5 especies diferentes) fueron identificadas usando detectores de ultrasonidos, 17 especies fueron detectadas durante la inspecci ó n de refugios, y 13 especies fueron capturadas usando redes de niebla. No obstante, la rarefacci ó n demostr ó que las redes de niebla tuvieron la mayor riqueza relativa al n ú mero de individuos capturados. Comparamos las frecuencias de aparici ó n de las especies identificadas con los 3 m é todos de muestreo y observamos que ciertas especies eran sobre muestreadas o infra muestreadas d ependiendo del m é todo de muestreo usado. Tambi é n se agruparon las especies en 3 gremios definidos por la preferencias en el tipo de refugio utilizado durante el verano. Una correlaci ó n altamente significativa entre el gremio y el m é todo de detecci ó n fue en contrada y los quir ó pteros de cavidades quedaron infra representados cuando solamente los detectores de ultrasonidos y las redes de niebla fueron utilizadas. Por otro lado, los quir ó pteros que utilizan grietas en rocas o en infraestructuras humanas, y los que utilizan refugios en á rbol, quedaron infra representados cuando solamente se inspeccionaron refugios. Creemos que para determinar la riqueza de las comunidades de quir ó pteros es necesario utilizar diversas t é cnicas y recomendamos la combinaci ó n de todo s los m é todos descritos arriba en futuros estudios sobre las comunidades de quir ó pteros. A CKNOWLEDGMENTS Bats were caught with permits from the Catalan (Ministeri del Medi Ambient i Habitatge) and in some cases were banded following the criteria established by (Ministerio de Medio Ambiente). The work was supported by the Generalitat de Catalunya, Diputaci ó de Barcelona, and Consorci del Parc natural de Collserola. We also thank the Natural Park staff of the Á rea Protegida del Montgr í i les Illes Medes, Parc Natural à , Parc Natural del Cap de è era and Parc Natural dels Ports, Parc Natural de Collserola, Parc del Foix, Parc Natural del Montnegre i el Corredor, Parc Natural de les Guilleries Savassona, and Parc Natural del Montseny. Fieldwork would not have been possible without the support of R. Ru í z Jarillo, X. Puig, A. Burgas, A. Ribas, F. Sol à R. Garcia, and D. Burgas. We also thank 2 anonymous reviewers for their useful comments on former versions of the manuscript. TABLE 1. Frequencies of occurrence of the 22 bat species and number of speci es detected by 3 bat sampling methods in a coastal Mediterranean area. Species Mist nets Roost surveillance Bat detectors Rhinolophus ferrumequinum 7.76 0.1 R. hipposideros 3.46 0.05 R. euryale 7.29 0.12 Myotis myotis 2.46 0.61 a M. blythii 2.36 0.02 M. nattereri 0.45 M. emarginatus 0.79 11.43 M. daubentonii 3.94 0.38 2.95 b M. capaccinii 0.01 Pipistrellus pipistrellus 20.47 0.24 29.22 P. pygmaeus 14.17 13.56 40.79

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 155 P. nathusii 0.01 P. kuhlii 3.15 0.19 4.68 Hypsugo savii 20.47 4.8 Nyctalus leisleri 7.09 1.15 N. noctula/N. lasiopterus 0.15 Eptesicus serotinus 6.3 0.69 4.36 Barbastella barbastellus 3.15 1.39 Plecotus austriacus 13.39 0.66 1.92 c P. auritus 3.15 Miniopterus schreibersii 1.57 51.37 0.01 Tadarida teniotis 7.72 Number of species 13 17 17 a Species pairs with M. blythii . b Species pairs with M. capaccinii . c Species pairs with P. auritus . F IG . 1. Standardized residuals after a log linear analysis showing A) bat species oversampled by roost surveys and unde rsampled by bat detectors and mistnetting, and B) species undersampled by roost surveys and oversampled by bat detectors and mistnetting (interaction of species x method: G = 12,842, d.f. = 42, P < 0.0001). All species showed significant differences in fre quencies of occurrence between methods. Positive residuals: oversampling of a species; negative residuals: undersampling of a species. Residuals marked with asterisk were not significantly different from zero. Some species are acoustic pairs in the case of bat detectors (see Table 1). F IG . 2. Standardized residuals after a log linear analysis performed with the 3 guilds based on summer roost preferences and the 3 sampling methods (interaction of guild x method: G = 9,679, d.f. 1 = 4, P < 0.0001). Positive r esiduals: oversampling of a guild; negative residuals: undersampling of a guild. All the residuals were significantly different from zero. F IG . 3. Frequencies of occurrence of stations with 0 9 species detected by all sampling methods. Statistical differe nces between methods for all categories were assessed by means of a log linear analysis with sampling methods (3 categories) and number of species detected (9 species; interaction of species richness x method: G = 47.45, d.f. = 18, P < 0.0001). Significant differences between categories are shown by P level. F IG . 4. Rarefied species accumulation curves showing number of species (mean 6 SD ) versus number of individuals or contacts detected by each sampling method. L ITERATURE C ITED A HL É N , I. 1990. Identific ation of bats in flight. Swedish Society Conservation of Nature and the Swedish Youth Association for Environmental Studies and Conservation. Katarina tryck Ab Press, Stockholm, Sweden. A HL É N , I., AND H. J. B AAGOE . 1999. Use of ultrasound detectors for bat studies in Europe: experiences from field identification, surveys and monitoring. Acta Chiropterologica 1:137 150. A NIMAL C ARE AND U SE C OMMITTEE . 1998. Guidelines for the capture, handling, and care of mammals as approved by the American Society of Mammal ogists. Journal of Mammalogy 79:1416 1431. A RTHUR , L., AND M. L EMAIRE . 1999. Les Chauves souris ma î tresses de la nuit. Delachaux et Niestl é , Biblioth è que du Naturaliste, Lausanne, Switzerland. A VILA F LORES , R., AND M. B. F ENTON . 2005. Use of spatial featur es by foraging insectivorous bats in a large urban landscape. Journal of Mammalogy 86:1193 1204. B ARATAUD , M. 1996. The world of bats. Sittelle Press, Mens, France. B ARATAUD , M. 1998. Inventaire au d é tecteur è res fr é quentant les zone s (Alpes, France). Le Rhinolophe 13:43 52. B ARCLAY , R. M. R. 1999. Bats are not birds: a cautionary note on using echolocation calls to identify bats. Journal of Mammalogy 80:290 296. B RITTINGHAM , M. C., AN D L. M. W ILLIAMS . 2000. Bat boxes as alternative roosts for displaced bat maternity colonies. Wildlife Society Bulletin 28:197 207. C IECHANOWSKI , ET AL . 2002. Bat fauna of the Hawa Lakeland Landscape Park (northern Poland).

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 156 Myotis 40:33 45. D E P AZ , O., AND J. B ENZAL . 1990. Clave para la identificaci ó n de los murci é lagos de la Pen í nsula Ib é rica (Mammalia, Chiroptera). Miscell à nia Zool ò gica 13:153 176. D UFFY , A. M., L. F. L UMSDEN , C. R. C ADDLE , R. R. C HICK , AND G. R. N EWELL . 2000. The efficacy of AnaBat ultra sonic detectors and harp traps for surveying microchiropterans in south eastern Australia. Acta Chiropterologica 2:127 144. F LAQUER , C., R. R U Í Z J ARILLO , AND A. A RRIZABALAGA . 2004. Aportaci ó n de nuevas citas a la fauna quiropterol ó gica de Catalu ñ a. Galemys 16:39 55. F LAQUER , C., R. R UI´Z J ARILLO , I. T ORRE , AND A. A RRIZABALAGA . 2005. First resident population of Pipistrellus nathusii (Keyserling and Blasius, 1839) in the Iberian Peninsula. Acta Chiropterologica 7:183 188. F LAQUER , C., I. T ORRE , AND A. A RRIZA BALAGA . 2007. Selecci ó n de refugios, gesti ó n forestal y conservaci ó n de los quir ó pteros forestales. Pages 465 484 in Conservaci ó n de la biodiversidad y gesti ó n forestal: su aplicaci ó n en la fauna vertebrada (J. Camprodon and E. Plana, eds.). Edicions de la Universitat de Barcelona, Barcelona, Spain. F LAQUER , C., I. T ORRE , AND R. R U Í Z J ARILLO . 2006. The value of bat boxes in the conservation of Pipistrellus pygmaeus in wetland rice paddies. Biological Conservation 128:223 230. G OTELLI , N. J., AND R. K. C OLWE LL . 2001. Quantifying biodiversity: procedures and pitfalls in the measurement and comparison of species richness. Ecology Letters 4:379 391. H AYES , J. P. 2000. Assumptions and practical considerations in the design and interpretation of echolocation monit oring studies. Acta Chiropterologica 2:225 236. H ELVERSEN , O. V. 1989. Bestimmungsschl ü ssel f ü r die Europ ä ischen Flederm ä use nach ä usseren Merkmalen. Myotis 27:41 60. J ABERG , C., AND A. G UISAN . 20 01. Model ing the distribution of bats in relation to landsca pe structure in a temperate mountain environment. Journal of Applied Ecology 38:1169 1181. L AMBERT , T. D., J. R. M ALCOLM , AND B. L. Z IMMERMAN . 2005. Variation in small mammal species richness by trap height and trap type in southeastern Amazonia. Journal o f Mammalogy 86:982 990. L " PEZ G ONZ Á LEZ , C. 2004. Ecological zoogeography of the bats of Paraguay. Journal of Biogeography 31:33 45. L OURENC¸ O , S. I., AND J. M. P ALMEIRIM . 2004. Influence of temperature in roost selection by Pipistrellus pygmaeus (Chiropte ra): relevance for design of bat boxes. Biological Conservation 119:237 243. M ENU , H., AND J. B. P OPELARD . 1987. Utilitsation des caracteres dentaires pour la determination des 4:1 88. M ITCHELL J ONES , A. J., AND A. P. M C L EISH . Conservation Committee, Peterborough, United Kingdom. M URRAY , K. L., E. R. B RITZKE , B. M. H ADLEY , AND L. W. R OBBINS . 1999. Surveying bat communities: a comparison between mist nets and AnaBat II bat detector system. Acta Chiropterologica 1:105 112. ARRELL , M. J., AND W. L. G ANNON . 1999. A comparison of acoustics versus capture techniques for the inventory of bats. Journal of Mammalogy 80:24 30. P ALMEIRIM , J. M. 1990. Bats of Portu gal: zoogeography and systematics. Miscellaneous Publications, Museum of Natural History, University of Kansas 82:1 53. P ALOMO , L. J., AND J. G ISBERT . 2002. Atlas de los Conservacio´n de la Naturaleza SECEM SECEMU, Madrid, Spain. P AUZA , D. H., AND N. P AUZIENE . 1998. Bats of Lithuania: distribution, status and protection. Mammal Review 28:53 67. R ANSOME , R., AND A. M. H UTSON . 1999. Revised action plan for conservation of the greater horseshoe bat ( Rhinolophus ferrume quinum ) in Europe. T PVS (99) 11 (rev.). Council of Europe, Strasbourg, France. R ICE , R. W. 1989. Analyzing tables of statistical test s. Evolution 43:223 225. R UCZY SKI , I., AND W. B OGDANOWICZ . 2005. Roost cavity selection by Nyctalus noctula and N. leisleri (Vespertilionidae, Chiroptera) in Bia1owie a Primeval Forest, eastern Poland. Journal of Mammalogy 86:921 930. R UCZY SKI , I., AND I. R UCZY SKA . 2000. Roosting si Nyctalus leisleri in Bia1owie a Forest preliminary results. Myotis 37:55 60. R USS , J. 1999. The bats of Britain and Ireland: echolocation calls, sound analysis, and species identification. Alana Ecology Books, Belfast, Ireland.

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 157 R USSO , D., AND G. J ONES . 1999. The social calls of Pipistrellus kuhlii (Kuhl, 1819): structure and variation (Chiroptera: Vespertilionidae). Journal of Zoology (London) 249:476 481. R USSO , D., AND G. J ONES . 2003. Use of foraging habitat by bat s in a Mediterranean area determined by acoustic surveys: conservation implications. Ecography 26:197 209. S CHOBER , W., AND E. G RIMMBERGER . 1996. Los murci é lagos de Espa ñ a y de Europa. Ediciones Omega, Barcelona, Spain. S ERRA C OBO , J. 1987. Els quir ò pters: rats penats. Pp. 284 311 in Amfibis, r è ptils i mam í fers. Hist ò ria natural dels Pa ï sos Catalans (R. Folch, ed.). Enciclopedia Catalana, Barcelona, Spain. Vol. 13. S IMMONS , N. B., AND T. M. C ONWAY . 2003. Evolution of ecological diversity in bats. Pp. 493 53 5 in Bat ecology (T. H. Kunz and M. B. Fenton, eds.). University of Chicago Press, Chicago, Illinois. S TEBBINGS , R. E., AND S. T. W ALSH . 1991. Bat boxes. Bat Conservation Trust, London, United Kingdom. S TEVENS , R. D., AND M. R. W ILLIG . 2002. Geographical e cology at the community level: perspectives on the diversity on New World bats. Ecology 83:545 560. T ORRE , I., A. A RRIZABALAGA , AND C. F LAQUER . 2004. Three methods for assessing richness and composition of small mammal communities. Journal of Mammalogy 85: 524 530. T UTTLE , M. D., D. A. R. T AYLOR , R. A. M EDELLI´N , AND S. W ALKER . 2000. Murci é lagos y minas. Bat Conservation International, Inc., Austin, Texas. V AUGHAN , N., G. J ONES , AND S. H ARRIS . 1997. Habitat use by bats (Chiroptera) assessed by means of a bro ad band acoustic method. Journal of Applied Ecology 34:716 730. W ALSH , A., C. M. C ATTO , T.M. H UTSON , P. A. R ACEY , P. R ICHARDSON , AND S. L ANGTON . final report 2001. Department for Enviro n ment, Food and Rural Affairs, Bristol, United Kingdom. W ALSH , A. L., AND S. H ARRIS . 1996. Factors determining the abundance of vespertilionid bats in Britain: geographical, land classes and local habitat relationships. Journal of Applied Ecology 33:519 529. W ICKRAMASINGHE , L. P., S. H ARRIS , G. J ONES , AND N. V AUGHAN . 2003. Bat activity and species richness on organic and conventional farms: impact of agricultural intensification. Journal of Applied Ecology 40:984 993. W ICKRAMASINGHE , L. P., S. H ARRIS , G. J ONES , AND N. V AUGHAN . 2 004. Abundance and species richness of nocturnal insects on organic and conventional farms: effects of agricultural intensification on bat foraging. Conservation Biology 18:1283 1292. W ILSON , D. E., AND D. M. R EEDER . 2005. Mammal species of the world: a ta xonomic and geographic reference. 3rd ed. Johns Hopkins University Press, Baltimore, Maryland. Z AR , J. H. 1996. Biostatistical analysis. 3rd ed. Prentice Hall, Inc., London, United Kingdom. Submitted 4 May 2006. Accepted 4 September 2006. Associate Edit or was Douglas A. Kelt.

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 158 Temporal Variation in Activity of Bats and the Design of Echolocation monitoring Studies by John P. Hayes J. Mamm ., 78(2): 514 524, 1997. I used Anabat II bat detectors to monitor echolocation calls of bats o ver two streams in the Oregon Coast Range for a total of 195 detector nights. Activity of bats was positively correlated with biomass of insects and minimum nightly temperature, and was negatively correlated with length of night; activity levels at the two streams were positively correlated. Activity of bats was not significantly correlated with either hours of moonlight or with phase of moon. Level of activity within a night generally peaked shortly after sunset with a second, smaller peak in activity shor tly before sunrise, but patterns varied substantially among nights. Total nightly activity at a site also varied substantially among nights, sometimes varying several fold on consecutive nights. To assess the implications of temporal variation in activity of bats on sampling, I randomly sampled subsets of the data using from 2 to 12 night sample periods and calculated mean levels of activity for each subset. For subsets with seven or more nights, > 60% of the subsets had means that were within 20% of the m ean of the entire dataset. Less than 50% of the subsets had means within 10% of the mean of the entire dataset for any number of nights subsampled. When comparing activity between sites, use of blocked or paired designs improved sampling efficiency by 20%. Failure to account for temporal variation in activity of bats when designing research projects and monitoring programs could result in biased estimates of activity of bats. Key words: bat detector, activity of bats, echolocation, activity patterns, tempo ral variation, sampling, statistical design Recently, there has been a surge of interest in studying habitat relationships of bats by monitoring echolocation calls using bat detectors (Barclay, 1991; Burford and Lacki, 1995; Crampton and Barclay, 1996; E rickson and West, 1996; Hayes and Adam, 1996; Krusic and Neefus, 1996; McAiney and Fairley, 1988; Parker et al., 1996; Thomas, 1988). This interest has been spurred, in part, by technological improvements in relatively low cost bat detectors. Use of bat de tectors holds promise for addressing questions concerning patterns of activity and use of habitat by bats, but the technique has limitations. One important limitation is that it is not possible to estimate population abundance using bat detectors; however, data collected using bat detectors can provide estimates of activity of bats. In addition, experimental approaches have not been standardized and considerations for design of studies have not been fully evaluated. Temporal variation in activity of bats m ay influence the design and interpretation of studies and monitoring programs using bat detectors. Activity patterns of bats may vary on a daily or seasonal basis in response to a variety of exogenous and endogenous factors, including abundance of insects (Anthony et al., 1981; Avery, 1985; Barclay, 1991; de Jong and Ahlen, 1991; , 1994; Crespo et al., 1972; Fenton et al., 1977; Morrison, 1978; Reith, 1982; Usman et al., 1980), air temperature (Anthony et al. , 1981; Audet, 1990; Avery, 1985; Kunz, 1973; Lacki, 1984; Maier, 1992; Ruedi, 1993; Rydell, 1991; Whitaker and Rissler, 1992), heavy rainfall (Bell, 1980; Fenton, 1970; Fenton et al., 1977; Kunz, 1973; Reudi, 1993), wind (Adam et al., 1994; Avery, 1985; O 1967; Rydell, 1991), relative humidity (Adam et al., 1994; Lacki, 1984), metabolic water balance (Hays et al., 1992; Speakman and Racey, 1989), energetic demands imposed by pregnancy (Anthony et al., 1981; Rued i, 1993; Swift, 1980), and interspecific competition (Kunz, 1973; Reith, 1980). Factors that are correlated with activity level differ among studies and may be area and species specific. If experimental and sampling designs do not adequately account fo r temporal variation, estimates of activity for an area could be biased, and apparent differences or similarities among areas could be an artifact of temporal variation. By understanding patterns and correlates of variation in activity of bats, design of r esearch and monitoring programs can be improved. In this paper I present information on temporal patterns of variation in activity of bats in two riparian areas in the Oregon Coast Range. Materials And Methods Field methods. I monitored activity of bats i n riparian areas of two third order streams in the Oregon Coast Range; Bark Creek (T11S, R7W, Sec. 30) and Buttermilk Creek (T10S, R8W, Sec. 31). The streams are ca. 14.5 km apart. Overstory vegetation in monitored areas was dominated by red alder ( Almus r ubra). Forest canopy

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 159 cover was 100% in most areas, and branches of alders interdigitated, creating the appearance of a tunnel of air space over the stream. I monitored activity of bats for 94 nights at Bark Creek and for 101 nights at Buttermilk Creek bet ween 29 June 1993 and 12 October 1994 using the Anabat II bat detector system according to methods described by Hayes and Hounihan (1994). Echolocation calls were recorded on audio tape as bats flew over or near a monitoring station. I defined each sequenc e of one or more echolocation pulses with < 1 s between sequential pulses as a pass by a bat (Fenton, 1970). Calls were recorded along with the time of day and a calibration tone to aid in later analysis. Bat detectors were set at a sensitivity of six to m inimize stream and insect noises and to eliminate detections of bats flying in adjacent habitats. Each monitoring station was within 3 m of the edge of the stream with the microphone of the bat detector facing parallel to the main axis of the stream. I sa mpled populations of insects for 89 nights at Bark Creek and for 87 nights at Buttermilk Creek between June 1993 and October 1994 using 10 watt black light traps (Bioquip, Santa Monica, CA) powered by 12 volt gel cells. Traps were set to operate for a 3 h period beginning 30 min after legal sunset using a 12 volt timer (Real Goods, Ukiah, CA). Insects were collected in alcohol, oven dried $ 24 h, and weighed. Preservation of invertebrates in alcohol decreases their dry weight biomass (Leuven et al., 1985), and, thus, estimates of dry mass may be biased and only should be considered as indices. I monitored minimum nightly temperatures at the bat monitoring stations using Hobo Temp monitors (Onset Instruments, Pocasset, MA). Analysis of activity levels and en vironmental correlates. An analysis of 1,879 passes recorded during 10 randomly selected nights at Bark Creek and at Buttermilk Creek revealed that > 99% of identifiable calls had characteristics typical of species of Myotis (Hayes and Adam, 1996). Because of similarities in characteristics of echolocation calls among species of Myotis in this geographical area, I did not attempt to categorize calls to species in this study. I used an index of activity (IA) as a measure of activity levels. For nights when b ats were successfully recorded throughout the night, IA is the total number of passes recorded. During nights with highest levels of activity, audio tapes were filled with calls of bats before the end of the night. To determine the IA for these nights, I a ssumed that the best estimate of total activity was a function of the number of passes recorded, the proportion of the night elapsed when the tape was filled, and the proportion of the total number of passes expected to occur during that portion of the nig ht. This approach is not ideal, as patterns of activity can vary among nights. However, this approach should provide a general index of activity that is acceptable for use of rank order statistical procedures. To determine patterns of activity within night s for use in calculating IA and for assessment of temporal pattern, I determined each night at Bark Creek for which audio tape were not completely filled with calls before the end of the night and for which at least 175 passes were recorded (n = 24 nights) . I restricted the analysis to these night because I assumed that the pattern of activity in these nights with relatively high levels of activity ($ 175 calls) would most closely reflect the pattern of activity on nights for which the tapes were filled wit h calls prior to the end of the night. To account for differences in length of night, activity was partitioned into 20 equal time intervals from sunset to sunrise these intervals varied from 26 to 41 min (0 = 29.7 min). The proportion of passes recorded in each interval was determined and the mean proportion for all these nights was calculated. For nights when the tape was filled with calls of bats before the end of the night, the IA was calculated by dividing the number of passes recorded by the mean propo rtion of passes recorded in that proportion of the night. I tested for correlations between nightly IA at Bark and Buttermilk creeks, and between IA at each site and length of night, hours of moonlight, phase of moon (expressed as a percentage of full moo n), dry mass of insects captured at the site, and minimum nightly temperature at the site using p . I also examined correlations between dry mass of insects and minimum nightly temperature. I determined statistical power of tests that resulted in non significant results using tables in Kraemer and Thiemann (1987). Because of significant correlations among variables, I examined partial correlations of activity of bats with dry mass of insects and with minimum nightly temperature. Effect of number of nights sampled. As activity of bats generally is greatest and most sampling typically occurs during the summer months, I examined data from June, July, and August at Bark Creek (1993, n = 24 nights; 1994, n = 22) and Buttermilk Creek (1993, n = 28; 1994 , n = 18) to determine the influence of number of nights sampled on estimates of activity of bats. I randomly

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 160 sampled from 2 to 12 nights subsets 100 times each from each of the four datasets and determined the mean nightly IA for each random sample. I th en determined the proportion of each 100 random samples that had means within 10, 20, 30, 40, and 50% of the mean computed using the corresponding complete dataset. All sampling and analyses were performed using the SAS statistical software package for per sonal computers (SAS Institute, Inc., 1985). Comparison of paired and independent sample designs. The number of samples necessary to achieve the same statistical power with paired and unpaired designs is a function of the variance estimates for the two de signs. An unbiased estimate of the variance for the paired design is the sample variance for the paired data, S 2 D . An unbiased estimate of the variance for the unpaired design is: 2S 2 p (S 2 p S 2 D )/(2 n 1). where, S 2 p = (S 2 1 + S 2 2 )/2, S 2 p is the pooled sa mple variance of the two populations, n is the sample size of each population, and S 2 1 and S 2 2 are the sample variance of the two populations (Snedecor and Cochran, 1980). I compared the relative efficiency of paired and independent sampling designs by examining the ratio of variances for the two designs. To account for differences in degrees of freedom in the two experimental designs, I compared variances adjusted for degrees of freedom by multiplying the variances by ( v + 3)/( v + I ), where v is the nu mber of degrees of freedom of the experimental design (Snedecor and Cochran, 1980). I determined S 2 p and S 2 D using the IA values for all nights when activity of bats was recorded at both sites. To eliminate the potential influence of low levels of activit y in winter months on estimates of variance, this analysis was repeated omitting data collected from November through April. Results And Discussion Temporal patterns of activity. Levels and patterns of activity varied substantially within nights, among ni ghts within seasons, among seasons, and between sites. Mean activity within a night had a bimodal distribution with a peak of activity shortly after sunset and a second, smaller peak just before sunrise (Fig. 1). This pattern is typical of many species of insectivorous bats (Erkert, 1982; Kunz, 1973; Maier, 1992; Taylor and O'Neill, 1988) and probably results from a period of initial foraging and drinking after emerging from day roosts, reduced activity during the middle of the night when bats are at night roosts, and a final bout of foraging and commuting activity before returning to day roosts (Kunz, 1974; Kunz et al., 1995). Figure 1 Although distribution of nightly activity tended to be bimodal, patterns of activity varied substantially among nights. D istributions of activity were bimodal on some nights (Fig. 2a), but frequently the second peak of activity was missing (Fig. 2b). On other nights, activity persisted at moderate levels throughout the night with multiple peaks (Fig. 2c), and occasionally th ere was little activity early in the evening, with increased activity later in the night (Fig. 2d). The reasons for this variability are not clear, and may be related to changes in abundance of insects, meteorological conditions, social factors, energetic needs of the bats, or some other factor. Variability in nightly patterns suggests that caution should be employed when interpreting data collected during small portions of the night. Variability due to changes in distributions of activity will increase sam ple variance, requiring larger samples for precise estimates, and increases the probability that incorrect inferences will be drawn if sites are inadequately sampled. Total activity also varied substantially among nights (Fig. 3). Levels of activity varied seasonally, but sometimes levels of activity on consecutive nights also differed by several fold. Bats were active throughout the year, but activity during winter months was uniformly low (Fig. 3). Low levels of activity during winter is typical for bats (Arlettaz, 1990; Avery, 1985; Brack and Twente, 1985; Hays et al., 1992; Speakman and Racey, 1989; Whitaker and Rissler, 1992). Reasons for activity in winter are controversial, and probably vary with species and conditions, but include

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 161 feeding (Avery, 19 85; Brigham, 1987), drinking (Speakman and Racey, 1989), or changing hibernacula (Whitaker and Rissler, 1993). Number of passes of bats recorded at Bark Creek (0 = 260.0 " 58.2) averaged 4.8X greater than at Buttermilk Creek (0 = 54.2 " 11.4). Despite th ese large differences, levels of activity at the two study sites were highly correlated (p = 0.613, n = 82, P < 0.001). Given the separation of the two streams (14.5 km) and the abundance of water sources and potential roost sites in the central Oregon Coa st Range, bats using Bark and Buttermilk creeks probably represent independent sets of individuals. Positive correlations in activity between the sites are likely the result of responses to similar environmental conditions at the two sites. Environmental correlates of levels of activity. Activity of bats was positively correlated with minimum nightly temperature at both Bark Creek (p = 0.643, n = 86 , P < 0.001) and Buttermilk Creek (p = 0.456, n = 94, P < 0.001). The relationship between minimum temperatur e and activity of bats was non linear. Activity decreased dramatically when minimum temperatures dropped below 4EC at Bark Creek or 0EC at Buttermilk Creek (Fig. 4). Although less pronounced, the IA was positively correlated with temperature when only nigh ts with minimum temperatures > 4EC were considered (Bark Creek: p = 0.321, n = 63, P = 0.01; Buttermilk Creek: p = 0.289, n = 66, P = 0.02). These findings are consistent with those of previous studies documenting the influence of temperature on activity o f bats (Anthony et al., 1981; Audet, 1990; Avery, 1985; Kunz, 1973; Lacki, 1984; Maier, 1992; Ruedi, 1993; Rydell, 1991; Whitaker and Rissler, 1992). Activity of bats was negatively correlated with number of hours in the night (Bark Creek: p = !0.513, n = 94, P < 0.001; Buttermilk Creek: p = !0.342, n = 101, P < 0.001), reflecting seasonal changes in levels of activity (Fig. 4). Activity of bats was positively correlated with dry mass of insects collected (Bark Creek: p = 0.481, n = 70, P < 0.001; Butterm ilk Creek: p = 0.388, n = 73, P < 0.001). Rautenbach et al. (1996) also found a significant relationship between abundance of insects and activity of bats. Dry mass of insects was significantly positively correlated with minimum nightly temperature (Bark C reek: p = 0.581, n = 85, P < 0.001; Buttermilk Creek: p = 0.698, n = 78, P < 0.001). Partial correlation coefficients for activity of bats and temperature while holding biomass of insects constant (Bark Creek: p = 0.509; Buttermilk Creek: p = 0.279) were h igher than those for activity of bats and biomass of insects while holding temperature constant (Bark Creek: p = 0.172; Buttermilk Creek: p = 0.110). This suggests that the relationship between levels of activity and temperature is stronger than that betwe en level of activity and biomass of insects, and that the apparent relationship between level of activity and biomass of insects may be due to the correlation of both with temperature. The distribution of partial correlation coefficients depends on the mul ti variate distribution function of the variables, and consequently P values can not be determined for non normal distributions (Conover, 1980). Activity of bats was not significantly correlated with P either phase of the moon (Bark Creek: p = 0.007, n = 94, = 0.95; Buttermilk Creek: p = 0.007, n = 101, P = 0.94) or number of hours of moonlight (Bark Creek: p = 0.122, n = 101, P = 0.24; Buttermilk Creek: p = 0.115, n = 101, P = 0.25). The statistical power of the tests s > 0.90 to detect correlations of p = 0.35 (at " = 0.05). Lack of statistical significance despite acceptable power suggests that any influence of moonlight on activity was slight in comparison with other factors. The absence of detectable relationships between activity of bats and moon light contrasts with several studies (Adam et al., 1994; Crespo et al., 1972; Fenton et al., 1977; Morrison, 1978; Reith, 1982; Usman et al., 1980). I did not consider cloud cover in my analysis; cloud cover may have confounded any relationship with phase of the moon, although I do not have evidence to support this hypothesis. Alternatively, dense canopy cover, such as that at Bark and Buttermilk

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 162 creeks, may minimize the influence of moonlight on activity of bats (Reith, 1982). Number of nights required fo r sampl ing. The large variation in levels of activity has consequences for sampling design that were evident from the results of subsampling the data (Table 1). As fewer nights are sampled, there is increased probability of obtaining mean estimates of acti vity that differ greatly from the mean values calculated using large datasets. For example, when subsamples consisted of only 2 nights, < 50% of the subsamples had mean numbers of passes within 30% of means calculated using the full dataset, whereas when s ubsamples included 7 nights this proportion increased to ca. 80%. About 3X more activity was recorded at Buttermilk Creek on 31 August 1994 (IA = 270) than on any other night at Buttermilk Creek during that season (on 8 June 1994, IA = 85), substantially increasing the observed variability in activity at Buttermilk Creek. Having 1 night with an unusually high or low level of activity in the sample decreases the proportion of subsets with means similar to means calculated using the full dataset. As a resul t, mean values of IA for subsampled data lacked precision and accuracy for the dataset for summer 1994 from Buttermilk Creek. To obtain less biased estimates of activity, more nights need to be sampled when variation is high. Although the occurrence of 1 n ight with atypical levels of activity strongly influenced analysis of this dataset, it may not be unusual, and may result from unusually large hatches of insects or other factors that increase local levels of activity. Assuming the means calculated from the full datasets represent the best available estimate of activity for a site during a particular season, low intensity sampling can result in under or overestimates of activity levels. Accurate and precise estimates of levels of activity derived using b at detectors will only be obtained through intensive sampling efforts. Results may differ regionally or in different habitats, but results from this study indicate that sampling a site fewer than 6 to 8 nights is likely to result in biased estimates of act ivity. Comparisons between sites. Although there are times when an estimate of mean activity at a site is useful, research often focuses on comparing levels of activity between two or more sites or types of habitat. For these comparisons, experiments can be constructed to test the null hypothesis that level of activity does not differ among sites; two typical designs to address questions of this type are completely randomized designs and randomized blocked designs. In a completely randomized design with tw o sites, a researcher randomly chooses nights to sample each site. In a randomized blocked design (or in the two site case, paired design), a researcher randomly chooses nights, but then samples each site on the same night and compares the difference in le vel of activity between sites

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 163 on a night by night basis. High correlation between levels of activity at Bark and Buttermilk creeks and the response of activity of bats to environmental factors suggest that designs that incorporate blocking or pairing may r educe experimental error and, therefore, be more efficient than completely randomized designs. Calculations of statistical power for completely randomized and randomized blocked designs differ only by the variance estimate used. The ratio of unbiased vari ance estimates resulting from these two designs, adjusted for differences in degrees of freedom in the analyses, can be used to determine the relative efficiency of the designs. Using a randomized blocked design to compare levels of activity between Bark a nd Buttermilk creeks was 20% more efficient than a completely randomized design for analyses of the entire dataset (adjusted variance estimate for completely randomized design = 87,920, for paired design = 73,216, n = 82) and for analyses excluding data co llected during winter months (adjusted variance estimate for completely randomized design = 64,373, for paired design = 53,958, n = 65). Thus, 20% fewer nights need to be sampled for a paired design to have the same statistical power as a completely random ized design. The paired approach also has the benefit that there is no assumption that variances of the two populations are equal, unlike the t test for independent samples (Snedecor and Cochran, 1980). Design of studies monitoring activity of bats must we igh the advantages of paired designs against the logistical difficulties imposed by collecting data from more than one site during the same time periods. Because of high temporal variability, statistical tests comparing levels of activity among sites are likely to have poor statistical power to detect small differences. As a result, a researcher may incorrectly fail to reject a null hypothesis and erroneously conclude that activity at two sites is not different. The risk of this improper inference is tempe red somewhat by the fact that habitat structure can have dramatic influences on amount of use by bats, resulting in several fold differences in levels of activity between habitat types (Hayes and Adam, 1996; Thomas, 1988). If subtle differences in levels o f activity are of interest, differences may only be detectable with intensive sampling efforts. Use of statistical power analysis will be helpful in determining the sampling effort required for any particular study. Applicability to other regions. All of the data used for this study were collected at two riparian areas in the Oregon Coast Range; the importance of temporal variation may differ in other regions or habitats. However, in the absence of extensive, site specific sampling to examine levels of tem poral variation in activity, the prudent approach is to assume that temporal variability is a substantial source of variation in levels of activity. Inadequate temporal replication can result in inaccurate and misleading findings. Sampling designs for echo location monitoring studies need to account for this variation to yield scientifically accurate, defensible results. Acknowledgments The staff of Starker Forests allowed access and granted permission for conducting this research on their lands. P. Houniha n assisted with field work, analysis of tapes, and database management. M. Adam assisted with field work and analysis of collection of insects. D. Bateman, E. Dent, E. Horvath, and K. Maas assisted with field work. Figures were prepared by S. Etessami. M. Adam, D. Larson, R. Steidl, D. Waldien, and J. O. Whitaker, Jr. provided helpful comments on earlier drafts of this paper. Financial support for this study was provided by the Coastal Oregon Productivity Enhancement Program, College of Forestry, Oregon Sta te University. Literature Cited Adam, M. D., M. J. Lacki, and L. G. Shoemaker. 1994. Influence of environmental conditions on flight activity of Plecotus townsendii virginianus (Chiroptera: Vespertilionidae). Brimleyana, 21:77 85. Anthony, E. L. P., M. H. Stack, and T. H. Kunz. 1981. Night roosting and the nocturnal time budget of the little brown bat, Myotis lucifugus , effects of reproductive status, prey density, and environmental conditions. Occologia, 51:151 156. ethologie du Cestoni, Tadarida teniotis (Chiroptera), dans les Alpes valaisannes (Sud ouest de la Suisse). Zeitschrift fur Saugetierkunde, 55:28 42. Audet, D. 1990. Foraging behavior and habitat use by a gleaning bat Myotis myotis (Chiroptera: Vespertilio nidae). Journal of Mammalogy, 71:420 427. Avery, M. I. 1995. Winter activity by pipistrelle bats. The Journal of Animal Ecology, 54:721 738. Barclay, R. M. R. 1991. Population structure of temperate zone insectivorous bats in relation to foraging behaviour and energy demand. The Journal of Animal Ecology, 60:165 178. Bell, G. P. 1980. Habitat use and response to patches of prey by desert insectivorous bats. Canadian Journal of Zoology, 58: 1876 1883.

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 164 Brack, V. Jr., and J. W. Twente. 1985. The duration of th e period of hibernation of three species of vespertilionid bats. I. Field studies. Canadian Journal of Zoology, 63:2952 2954. Brigham, R. M. 1987. The significance of winter activity by the big brown bat ( Eptesicus Fuscus ): the influence of energy reserves . Canadian Journal of Zoology. 65:1240 1242. Burford, L. S., and M. J. Lacki. 1995. Habitat use by Corynorhinus townsendii virginianus in the Daniel Boone National Forest. The American Midland Naturalist, 134:340 345. Conover, W. J. 1980. Practical nonpara metric statistics. Second ed. John Wiley & Sons. New York. 493 Pp. Crampton, L., and R. M. R. Barclay. 1996. Habitat selection by bats in fragmented and unfragmented aspen mixedwood stands of different ages. Pp. 238 259, in Bats and Forests Symposium, Octo ber 19 21, 1995 (R. M. R. Barclay and R. M. Brigham, Eds.). British Columbia Ministry of Forests, Research Branch, Victoria, Canada. Working Paper, 23:1 292. Crespo, R. F., S. B. Linhart, R. J. Burns, and G. C. Mitchell. 1972. Foraging behavior of the comm on vampire bat related to moonlight. Journal of Mammalogy, 53:366 368. De Jong, J., and I. Ahlen. 1991. Factors affecting the distribution pattern of bats in Uppland, Central Sweden. Holarctic Ecology, 14:92 96. Erickson, J., and S. West. 1996. Managed for ests in the western Cascades: the effects of seral stage on bat habitat use patterns. Pp. 215 227, in Bats and Forests Symposium, October 19 21, 1995 (R. M. R. Barclay and R. M. Brigham, Eds.). British Columbia Ministry of Forests, Research Branch, Victori a, Canada, Working Paper, 23:1 292. Erkert, H. G. 1982. Ecological aspects of bat activity rhythms. Pp. 201 242, in Ecology of Bats (T. H. Kunz, Ed.). Plenum Publishing Corporation, New York. 425pp. Fenton, M. B. 1970. A technique for monitoring bat activi ty with results obtained from different environments in southern Ontario. Canadian Journal of Zoology, 48:847 85 1. Fenton, M. B., N. G. H. Boyle, T. H. M. Harrison, and D. J. Oxley. 1977. Activity patterns, habitat use, and prey selection by some African insectivorous bats. Biotropica, 9:73 85. Hayes. J. P., and M. D. Adam. 1996. The influence of logging riparian areas on habitat use by bats in western Oregon. Pp. 185 198, in Bats and Forests Symposium, October 19 21, 1995 (R. M. R. Barclay and R. M. Brigh am, Eds.). British Columbia Ministry of Forests, Research Branch, Victoria, Working Paper, 23:1 292. Hayes, J. P, and P. Hounihan. 1994. Field use of the Anabat II bat detector system to monitor bat activity. Bat Research News, 35:1 3. Hays, G. C., J. R. S peakman, and P. I. Webb. 1992. Why do brown long eared bats ( Plecotus auritus ) fly in winter? Physiological Zoology, 65:554 567. Kraemer, H. C., and S. Thiemann, 1987. How many subjects? Sage Publications Ltd., Newbury Park, California, 120pp. Krusic R., a nd C. Neefus. 1996. Habitat association of bat species in the White Mountain National Forest. Pp. 185 198, in Bats and Forests Symposium, October 19 21, 1995 (R. M. R. Barclay and R. M. Brigham, Eds.). British Columbia Ministry of Forests, Research Branch, Victoria, Working Paper, 23:1 292. Kunz, T. H. 1973. Resource utilization: temporal and spatial components of bat activity in central Iowa. Journal of Mammalogy. 54:14 32. -1974. Feeding ecology of a temperate insectivorous bat ( Myotis velifer ). Ecology, 55:693 711. Kunz, T. H., J. O. Whitaker, Jr., and M. D. Wadaroll. 1995. Dietary energetics of the Mexican free tailed bat Tadarida brasiliensis during pregnancy and lactation. Occologia. 101:407 415. Lacki, M. J. 1984. Temperature and humidity induced shi fts in the flight activity of little brown bats. Ohio Journal of Science, 84:264 266. Leuven, R. S. E. W., T. C. M. Brock, and H. A. M. van Druten. 1985. Effects of preservation on dry and ash free dry weight biomass of some common aquatic macro invertebr ates. Hydrobiologia, 127: 151 159. Maier, C. 1992. Activity patterns of pipistrelle bats ( Pipistrellus pipistrellus ) in Oxfordshire. Journal of Zoology (London), 228:69 86. McAiney, C. M., and J. Fairley. 1988. Habitat preference and overnight and seasonal variation in the foraging activity of lesser horseshoe bats. Acta Theriologica, 33:393 402. Morrison, D. W. 1978. Lunar phobia in a Neo tropical fruit bat Artibeus jamaicensis (Chiroptera, Phyllostomatidae). Animal Behaviour, 26:853 855. O'Farrell, M. J., and W. G. Bradley. 1970. Activity patterns of bats over a desert spring. Journal of Mammalogy, 51:18 26. O'Farrell, M. J., W. 0. Bradley, and 0. W. Jones. 1967. Fall and winter bat activity at a desert spring in southern Nevada. The Southwestern Naturalis t, 12:163 171. Parker, D., J. Cook, and S. W. Lewis. 1996. Effects of timber harvest on bat activity in southeastern Alaska's temperate rainforests. Pp. 277 292, in Bats and Forests Symposium, October 19 21, 1995 (R. M. R. Barclay and R. M. Brigham, Eds.). British Columbia Ministry of Forests, Research Branch, Victoria, Working Paper, 23:1 292. Rautenbach, I. L., M. B. Fenton, and M. J. Whiting. 1996. Bats in riverine forests and woodlands: a latitudinal transect in southern Africa. Canadian Journal of Zool ogy, 74:312 322.

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 165 Reith, C. C. 1980. Shifts in times of activity by Lasionycteris noctivagans . Journal of Mammalogy, 61:104 108. -1982. Insectivorous bats fly in shadows to avoid moonlight. Journal of Mammalogy, 63:685 688. Ruedi, M. 1993. Variations de la frequentation de gites nocturnes par Myotis daubentoni pendant la periode de reproduction. Role des precipitations et de la temperature. Mammalia. 57:307 315. Rydell, J. 1991. Seasonal use of illuminated areas by foraging northern bats Eptesicus nilssoni. Holarctic Ecology, 14:203 207. SAS Institute, Inc. 1985. SAS procedures guide for personal computers, version 6 edition. Sas Institute Inc. Cary, North Carolina, 373 Pp. Snedecor, G. W., and W. G. Cochran. 1980. Statistical Method. Iowa State University P ress, Ames, 507 Pp. Speakman, J. R., and P. A. Racey. 1989. Hibernal ecology of the pipistrelle bat: energy expenditure, water requirements and mass loss, implications for survival and the function of winter emergence flights. The Journal of Animal Ecology , 58:797 813. Swift, S. M. 1980. Activity patterns of pipistrelle bats ( Pipistrellus pipistrellus ) in North east Scotland. Journal of Zoology (London), 190:285 295. Taylor, R. J., and M. G. O'Neill. 1988. Summer activity patterns of insectivorous bats and their prey in Tasmania. Australian Wildlife Research, 15:533 539. Thomas, D. W. 1988. The distribution of bats in different ages of douglas fir forests. The Journal of Wildlife Management, 52:619 628. Usman, K., J. Habersetzer, R. Subbaraj, G. Gopalkrishna swamy, and K. Paramanadam. 1980. Behaviour of bats during a lunar eclipse. Behavioral Ecology and Sociobiology, 7:79 81. Whitaker. J. O., Jr., and L. J. Rissler. 1992. Winter activity of bats at a mine entrance in Vermillion County, Indiana. The American M idland Naturalist. 127:52 59. -1993. Do bats feed in winter? The American Midland Naturalist, 129:200 203. Submitted 26 February 1996. Accepted 22 July 1996. Associate Editor Was Edward J. Heske. Table 1. Percentage of random sam ples having mean indices of activity (IAs) within 10 50% of the mean of the entire dataset. Values represent means and ranges (in parentheses) for datasets partitioned by site and year ( n = 4); data were randomly sampled 100 times for each 2 to 12 night s ample period for each site and year. For each dataset, comparisons were made with the mean IA for all nights at the site and year. Percentage deviation from mean estimate calculate d from full datasets Number of nights in subsample .10 .20 .30 .40 .50 2 19.0 (13 21) 31.8 (23 36) 47.8 (40 54) 57.8 (47 67) 72.5 (67 79) 3 20.5 (19 26) 43.2 (40 48) 58.0 (53 61) 73.0 (65 76) 82.2 (76 86) 4 21.2 (17 24) 41.3 (39 45) 62.8 (56 69) 77.0 (72 85) 86.2 (78 93) 5 27.2 (24 32) 48.8 (39 59) 69.2 (52 78) 83.8 (74 93) 88.2 (85 99) 6 31.0 (22 36) 52.2 (38 63) 63.8 (54 84) 86.0 (76 94) 94.2 (85 99) 7 29.8 (14 40) 61.2 (55 69) 80.5 (70 90) 91.8 (90 94) 97.8 (96 100) 8 30.5 (14 38) 62.8 (42 78) 83.2 (70 96) 97.0 (92 100) 99.0 (97 100) 9 33.0 (12 42) 67.8 (43 84) 91.5 (82 96) 98.5 (96 100) 99.8 (99 100) 10 39.5 (14 50) 68.2 (51 80) 90.8 (96 98) 98.0 (94 100) 100 (100) 11 33.5 (17 42) 76.0 (58 84) 96.5 (94 98) 100 (100) 100 (100) 12 46. 8 (29 58) 85.8 (80 94) 97.5 (96 99) 100 (100) 100 (100)

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 166 Transmitter Attachment for Small Insectivorous Bats (< 30 g) by Dr. Mark Brigham and Holohil Systems Ltd. Retrieved from: (March 17, 2008) A commonly used "rule" for working with flying animals is to keep the mass of the transmitter AND adhesive below 5% of body mass. This means that the smallest tag currently produced by Holohil (0.35g LB 2N) should not be attached to bats weighing less th an 7.0g. This rule may be bent (slightly) for the purpose of finding roost sites as there is little question that bats can carry heavier loads. However, for studies of roost preference, foraging behaviour, etc. it is my opinion that the 5% rule should be u sed. See Aldridge and Brigham, 1988 J. Mammalogy. It is important to emphasize that the rule represents a maximum transmitter load and in reality the smaller the transmitter, the less likely it is that an animal's behaviour will be affected. Transmitters s hould be attached to the area between the shoulder blades so that the bats cannot use their hind feet to pull off the tag. The adhesive I find works best is Skin Bond® (see note below). For bats with short fur (e.g., Eptesicus), transmitters seem to remain attached best if the fur is not clipped. The length of the fur, rate of growth, oiliness and even geographic location all seem to contribute to successful attachment. I suggest that at the beginning of a study, attach several tags with and without clippin g fur to see what works best. When applying the adhesive use a very thin layer on both the transmitter and the bat. Remember that adhesive also contributes to the mass of the transmitter package. Let stand for about 5 minutes until the glue bubbles, then a ffix the tag and hold it for a further 5 minutes. Frost the fur around the edge of the transmitter. At this point the initial setting of the glue will have occurred. It is now important to prevent the bat from scratching at and potentially loosening the ta g before the glue fully sets. I recommend holding the bat for another 10 30 minutes to make sure that the glue has set completely before releasing the animal. Note: Skin Bond® has recently changed its formulation and is no longer suitable for use. It's b onding time is much less than the original formulation. Do NOT use the surgical skin bond which is a methacrylate adhesive (Crazy Glue). We now suggest using Torbot Bonding Cement. Its adhesive properties are similar to the original Skin Bond® recommende d by Dr. Brigham above. It can be ordered through their website at: Another latex based adhesive that can be used is Eyelash Cement. Instead of a hexane solvent base, this material has a proprietary aqueous solvent base. A flexible formul ation of woodworking contact cement is being used by Australian researchers with good results in extremely wet conditions. Holohil Systems Ltd. 112 John Cavanaugh Drive Carp, Ontario, Canada K0A 1L0 Tel: 613 839 0676 Fax: 613 839 0675 E mail: info@holoh

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 167 Injuries to Plecotus townsendii from Lipped Wing Bands by Elizabeth D. Pierson and Gary M. Fellers. Bat Research News , Vol. 34, No. 4, pp. 89 91 In two occasions, the Pacific western big eared bat, Plecotus townsendii tow nsendii , has been banded as part of an ecological study in Marin County, California. We found that 3 mm lipped bands, of the design used extensively in Britain and known to be suitable for other North American species, caused significant and potentially fa tal injuries to > 11% of the recaptured sample. Our data also indicate that bands may cause a decrease in survivorship. We stopped using these bands on P. townsendii and have removed bands from all recaptured animals. Introduction Banding has been an imp ortant research tool in bat population studies for over 75 years (Hitchcock, 1957) and has been a source of continuing investigator concern. Initially when unlipped, metal, bird leg bands were the primary option, attention focused on the wing injury rate o f Tadarida brasiliensis and several other species (Hitchcock, 1957; Davis, 1960; Herreid et al., 1960). Although there appeared to be fewer wing injuries after introduction of lipped bat bands (Herreid et al., 1960), some populations, particularly in hiber nacula, showed significant declines in apparent response to the disturbance caused by banding activities (Davis and Hitchcock, 1965; Stebbings, 1969, 1978; Tuttle, 1979; Barclay and Bell, 1988). Although many bat researchers still observe the informal ban on disturbing hibernacula, increasing numbers of biologists are banding bats during summer, yet there is little discussion addressing the unresolved consequences of banding per se. Serious difficulties with banding a P. townsendii population in California lead us to suggest that there is the need for more dialogue on the effects of banding, particularly comparative assessments of different band materials and shapes (e.g., metal vs. plastic bands) and evaluations of species specific responses to banding. M ethods and Results On 9 October 1992, a total of 118 P. t. townsendii was captured at a roost site, which had been under study for six years. This number represented approximately 95% of the bats present. Each bat was sexed, weighed, measured for forearm l ength, and evaluated for tooth wear and reproductive condition. Each bat was fitted with a 3 mm, lipped, alloy band issued to the British Mammal Society by Lambournes Ltd. of England. The band was placed over the forearm and manually squeezed shut (without banding pliers) so that it would slide freely along the arm. The band was not loose enough, however, for the metacarpals to slip under the lips and become caught when the wing was folded. On 21 September 1993, 30 bats were netted in the evening as they e xited the roost. One of these had been banded in 1992. As before, each bat was sexed, weighed, measured, and evaluated for tooth wear and reproductive condition. All bats that had not been banded previously were fitted with similar lipped bands (2.8 mm dia meter the new equivalent to 3 mm bands) obtained directly from Lambournes Ltd. There was no sign of wing injury to the single bat that had been banded the previous year. On 8 October 1993, 111 bats were captured at the same roost. As in 1992, this represe nted approximately 95% of the bats present. Of the bats captured, 51 were recaptures from 1992 and 11 were recaptures from the previous month. All bats were processed as before. We found seven bats that had wing injuries associated with bands. One of these had been banded only 17 days before. This represented an injury rate of 11.8% (6/51) for the 1992 recaptures and 9.1 % (1/11) for the 1993 sample. For the one bat that had been banded 17 days before, the band was lodged at the distal end of the forearm. There was no swelling, but the skin under the band was abraded and had been bleeding. There was a somewhat roughened wing area, proximal to the band that held the band in place. It appeared that the band would not have come free on its own, and quite likel y, the injury would have progressed. The five injured bats originally banded in 1992 had considerable swelling around the band and adjacent 2 4 mm of forearm. The area was infected, and even modest movement of the band caused puss to be expressed. Each ba nd was carefully removed, revealing an area devoid of skin. In one case, the band had become embedded at the proximal end of the forearm, whereas the others were at the distal end. In three cases, the band had caused a small hole in the wing with the lippe d portion penetrating the membrane and allowing the band to completely encircle

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 168 the forearm. Although penetration of the wing membrane occurs with some frequency in banding studies, such injuries frequently are reported as having healed or callused over (H effeid el al. 1960). This was not the case for any P. townsendii that we observed. All animals were carefully inspected for signs of earlier band injury (such as scarring) that had healed or injury from bands that had somehow been removed. No such sign was detected. Discussion The most direct way to evaluate impacts from banding is to assess the percentage of a recaptured sample that shows wing injury. In our case, not only did an unacceptably high percentage (11.8%) of our recaptured sample show injury, b ut all injuries were active and thus judged to be potentially fatal. The fact that no bats had scarring to indicate healed wounds added support to the hypothesis that the bats do not recover from these injuries. Although most animals had been banded for a year, the six wounds we observed were in various stages of infection, suggesting an ongoing problem and an annual mortality rate that is likely much higher than the observed injury rate. We had reason to believe that band injuries would be minimal. Lambou were lighter weight and smoother edged than any used with virtually no sign of injury on large numbers of Myotis yumanensis (3.0 mm size) and Antrozous pallidus (4.0 mm si ze) (W. E. Rainey and E. D. Pierson, unpubl. data). Though there are suggestions in the literature that some species are more sensitive to banding than others (e.g., Hitchcock, 1957), this matter has been give little attention. Reports of band injuries wi th P. townsendii are variable. Davis (1960) suggests that P. townsendii may be among those species most prone to band injury. This view is supported by the experience, in Oregon, of S. Cross and M. Perkins (pers. comm.), who banded very few individuals but experienced a sufficiently high injury rate with lipped U. S. Fish and Wildlife Service bands that they ceased banding P. townsendii . On the other hand, Pearson et al. (1956) had very low injury rates (< 2%) using unlipped U. S. Fish and Wildlife Service bands (O. P. Pearson and A. K. Pearson pers. comm.). P. Leitner (pers. comm.), using 4.0 min (size 2) unlipped USFWS bands, had comparably low injury rates on another P. townsendii study in northern California, with 7 out of 391 recaptures (1.8%) having em bedded bands. Likewise, Stebbings (1966) had high (> 70%) survivorship and almost no sign mm lipped bands in England on Plecotus auritus a crevice dweller that shows marked behavioral differences from its North American congener. Why P. townsendii may be more prone to band injury than some other species from lipped metal bands is not clear, but we offer several observations that may provide a partial explanation. First, P. townsendii does not appear to gnaw on bands as other species do. We found no tooth marks nor other signs of wear on the bands and no differential tooth wear on the bats that could be attributed to band chewing. Chewing behavior, while having potentially negative consequences, such as accelerated tooth wear, may be advantageous in keeping bands from lodging on the forearm. Our observations indicate that P. townsendii may not attempt to dislodge bands that are stuck. In one early stage infection, the band moved with only a slight application of pressure a nd could almost certainly have been dislodged by the bat with only a modest amount of chewing. Additionally, P. townsendii seems to have especially thin wing membranes. Though we have not quantified this, the wings appear to be more delicate than those of other bats we have handled, including almost all genera present in the western United States. If this is an accurate perception, injuries from bands that penetrate the wing membrane might be more likely in this species. Also, the wings have a sticky quali ty we have not observed in other bats. The bands on recaptured animals and the wings of all animals were covered with a sticky orange substance, which when removed with a cotton swab, appeared identical to secretions from the rostral glands. The stickiness of this secretion may play some role in inhibiting free movement of the band. An injury rate of > 11% is clearly too high for any species. It was of special concern for this colony because it represents one of only four known for P. t. townsendii along t he California coast. This subspecies is a Category 2 Candidate for listing under the Federal Endangered Species Act. Our results lead us to conclude that, unless contrary data are available, other workers should not use this band type on P. townsendii. Whe ther some other banding protocol could work needs to be explored. D. Saugey (pers. comm.) has been using plastic bird leg bands (A.C. I. Hughes), individually filed to increase the gap, on P. rafinesquii. Preliminary results suggest

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 169 acceptably low injury r ates. He and coworkers, however, observed embedding when unfiled plastic bands were used. This is congruent with observations by one of us (EDP) of an embedded band on an individual that had been banded with a plastic band in southern California. We also n ote that R. E. Stebbings (pers. comm.) discontinued use of plastic bands over 20 years ago due to high injury rates (partly due to band shrinkage over time) for all species tested. We suggest that before initiating a banding study using plastic bands inves tigators contact both R. E. Stebbings and D. Saugey. One of us (EDP) and W. Rainey tried and subsequently rejected the use of bead necklaces (Barclay and Bell 1988) on another population, because the combined weight of the chain and band exceeded the 5% rule. Transponders may offer a viable alternative to banding, though the large size of even the smallest implants needs to be considered. We are open to the possibility that our banding technique was somehow at fault, although the absence of similar probl ems for other taxa banded in the same manner argues against investigator error. It is also possible that we should have used a larger size (3.5 mm) band. The 3 mm band is used routinely, however, on comparably sized Plecotus in Britain and appeared to fit well on our study animals moving freely, with space around the forearm. Since it seemed to be the lip that first became lodged, it is not clear that a larger band, which is more than twice as heavy (105 vs. 43 mg), would have alleviated the problem. We re commend that until it can be established that a particular band causes no more than minimal injury, banding of P. townsendii and other potentially sensitive species be limited to studies in which the impacts of banding can be evaluated directly. Since rate s of recapture are generally low for bats netted in foraging areas, studies would probably need to focus on bats at known roost sites. Such research would need to be designed carefully to reduce the possibility of undue disturbance, especially for P. towns endii , which is known to be so sensitive to human disturbance. Acknowledgments We thank P. Winters and C. Scott for their assistance in nursing injured animals back to health. J. Fellers and W. Rainey provided helpful comments on the manuscript. Banding w as carried out under a permit and Memorandum of Understanding issued to E. D. Pierson by California Department of Fish and Game. Literature Cited Barclay, R. M. R., and G. P. Bell. 1988. Marking and observational techniques. Marking and observational tech niques. Pp. 59 76 in Ecological and behavioral methods for the study of bats (T. 1 1. Kunz, ed.). Smithsonian Institution Press, Washington, D.C., 533 pp. Davis, W. II. 1960. Band injuries. Bat Banding News, 1:1 2. Davis, W. II., and H. B. Hitchcock. 1965. Biology and migration of the bat, Myotis lucifugus, in New England. J. Mammal., 46:296 313. Hereid, C. F., R. B. Davis, and H. L. Short. 1960. Injuries due to bat banding. J. Mammal., 41:398 400. Hitchcock, H. B. 1957. The use of bird bands on bats. J. Ma mmal., 38:402 405. Pearson, O. P., Koford, M. R., and A. K. Pearson. 1952. Reproduction of the lump nosed bat Corynorhinus rafinesquei in California. J. Mammal., 33:273 320. Stebbings, R. E. 1966. A population study of bats of the genus Plecotus. J. Zool., Lond., 150:53 75. 1969. Observer influence on bat behavior. Lynx, 10:93 100. 1978. Marking bats. Pp. 81 94 in Animal Marking (R. Stonehouse, ed.). Univ. Park Press, Baltimore, Maryland. Tuttle, M. B. 1979. Status, causes of decline, and management of endangered gray bats. J. Wildl. Manage., 43:1 17. Tuttle, M. B., and D. Stevenson. 1982. Growth and survival of bats. Pp. 105 150 in Ecology of bats (T.H.Kunz, ed.).Plenum Press, New York, 425 pp.

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 170 Educational Guidelines by Amanda Lollar and Barbara Sch midt French Reprinted with permission from: Captive Care and Medical Reference for the Rehabilitation of Insectivorous Bats , 1998. Bat World Publications, Mineral Wells, TX. 329 pages. Educating the public is one of the most outstanding contributions tha t can be made towards the conservation of bats as a whole. The use of live bats for educational programs has substantial value in influencing public opinion. However, a healthy balance should be established during these programs between teaching the import ance of bat conservation and fully communicating to the audience the potential dangers of handling wild animals. Rabies in wild mammals is of particular concern. It is important that both children and adults understand the possible consequences of handling potentially infected wildlife. North American bats are very small, possibly making them appear harmless to adults and children who might pick them up. Every year incidents are reported throughout the United States involving people (particularly children) who have inappropriately interacted with grounded bats. Although the majority of bats are not rabid, a certain percentage of those handled by the public will have contracted the rabies virus. Public hysteria following some incidents involving human/bat int eractions has resulted in the destruction of entire bat colonies. For these reasons, the principal purpose of educational programs should be to deliver accurate information about bats in a manner that protects both bats and humans. PROTOCOL 1. The use of liv e bats for educational purposes should be limited to licensed wildlife rehabilitators, educators, and research biologists. The authors recommend that these individuals be previously immunized against rabies and receive boosters when appropriate so that the y maintain an acceptable titer. The audience should also be informed that the presenter has received the recommended pre exposure rabies immunizations in order to work with mammalian wildlife. 2. The presenter should strive for a well groomed, professional a ppearance. 3. Bats should never be treated in any manner consistent with generally recognized treatment or care given to domestic pets. Petting, kissing or similar demonstrations of affection towards bats during public programs is highly inappropriate. 4. Pres enters should always refer to themselves as 5. Wildlife rehabilitators, educators, and researchers utilizing indigenous species of bats in educational programs should be permitted or licensed to handle bats by their state wildlife agency. Those using non indigenous species in educational programs should have an USDA exhibitor's license. It is recommended that permits and/or licenses be prominently displayed during all programs. 6. Presenters should strive to produce a program that is both educational and entertaining. An interactive question and answer program is often more conducive to learning than a lecture. To create a pleasant atmosphere, presentations can include amusing and humorous bat facts in combination with more serious ones. Laughter combined with learning may help to relax apprehensive audiences unfamiliar with bats. Entertaining and/or amazing bat facts are perhaps those most likely to be remembered by the audience and recounted to others, thereby furtheri ng your educational efforts. SUGGESTIONS FOR DISPLAYS 1. Include a display board depicting both indigenous and non indigenous bat species. Photographs and information about local bat species will be of particular interest to your audience. 2. All displays sho uld include a message on the importance of not approaching wild animals. Any literature to be distributed that addresses the benefits of bats should also include a warning to never touch bats. 3. Display cages, display boards, and literature placed on tables should be arranged neatly. Keep

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 171 the area uncluttered during presentations. Literature that will be available to the audience should be placed on a separate table from the one where display cages are situated (or in the area farthest from the display cages if a separate table is not available). This precaution minimizes stress to the bats by reducing traffic near their cages. 4. The use of a cam corder, RF modulator, tripod, and television is of great value for educational bat programs, particularly when deal ing with large audiences and/or limited space. The image of a bat can be enlarged when it is projected onto a television screen. The cam corder also serves to permanently record programs for both critical self review and documentation that animals were not touched by the public during presentation. BATS USED FOR EXHIBITION 1. Bats used for educational programs should either be non releasable indigenous species or non indigenous species. Non releasable status is assigned to orphans, captive born bats, and non suffering permanently injured bats. Although they may be caged with other bats, indigenous bats should have resided in captivity for at least one year without being exposed to any new bats during that time. Bats should not be on display for more than 30 m inutes a day. (It is not humane to subject insectivorous bats to permanent display.) 2. Use of both foliage roosting and crevice dwelling insectivorous bats, as well as frugivorous bats, is beneficial for demonstrating ecological diversity (e.g., differences in body size, shape, color, and how this is related to roosting and dietary habits). However, excellent presentations can be given utilizing only one or two individuals of the same bat species when a variety is not available. 3. Bats should be familiar with their handler and should have developed a sense of trust before being utilized for public presentations. Bats that trust their handler will respond to and during times of stress. Bats that have not become accust omed to their handler will be noticeably frightened during educational programs and should not be used for public viewing. 4. Bats used for display should be conditioned prior to the presentation. Conditioning should include familiarizing the bat with both t he display cage and transport carrier. Food rewards can be used throughout the conditioning period so that the bats develop positive associations with display cages. 5. Solitary bats (like many of the foliage roosting species) can be conditioned and displaye d singly during presentations. It is preferable, however, that colonial species be accompanied by permanent roost mates both during the conditioning period and educational presentations. 6. Bats should be left in the transport carrier and placed in an area i naccessible to the public after reaching the program area. Bats should remain undisturbed in the carrier in this area while displays and handouts are organized. Bats should be removed from the carrier and placed into a covered display cage before the audie nce arrives for the presentation. When the cage is uncovered for viewing, the bat may be given food rewards. After public viewing, display cages should be covered again. 7. Although educators have displayed bats by hand for many years during presentations, it is preferable that audiences view bats that are contained within a display cage. Bats that have been conditioned to being displayed by hand over a long period of time may not adjust to confinement in display cages, however. Some authorities recommend th at gloves be worn if bats are displayed by hand because a conflicting message may be sent to the audience if wild animals are handled with bare hands. 8. Presenters should remain next to the cage while bats are being viewed by the audience. Close up viewing of the bat works best if allowed only at the conclusion of a presentation. Encourage the audience to file by for viewing and to leave about one foot of space between them and the table. In addition, they should be told to not lean against the table towards the cage or to touch the cage. Children should be told to keep their hands in their pockets or behind their backs as they walk

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 172 by. During this time, a distance of two feet should be maintained between the display cage and the audience. This can be accompl ished by placing the cage in the center back area of the table so that l foot (30cm) or more of empty table space is created along the front and sides of the cage. 9. Never allow anyone to touch a bat in any way whatsoever. A bat that has been touched by an unauthorized individual may be subject to euthanasia and rabies testing by local health authorities regardless of the nature of the contact or the period of time the bat has remained in captivity. 10. Bats must never be permitted to fly or otherwise be loose during public programs. TRANSPORT CARRIERS AND DISPLAY CAGES 1. Use a transport carrier, rather than the display cage, for transporting bats to and from facilities where presentations will take place. Carriers should be appropriately modified so that they ca n be secured in vehicles with a seat belt. Carriers should be padded on the inside and covered with a cloth on the outside. Neither transport carriers nor display cages containing bats should be handled by anyone other than the presenter. 2. Display cages sh ould have surfaces that allow bats to hang upside down. If a plexiglass animal case is used, three of the four sides and the ceiling should be covered with nylon or plastic (not wire) screen to provide appropriate roosting surfaces. (Bats are unable to gri p plastic surfaces and may slip and fall, causing wrist or wing injury.) Screened, wooden frame display cages should be screen with no more than a 1/6" (4mm) mesh for small insectivorous bats. For larger bats such as flying foxes, ½" ( 13mm) plastic mesh should be used for the inner layer only. There should be a 1" (25mm) space between the two layers of screen. This space and the small mesh used for the outer layer will ensure that bats hanging close to the inside scr een or mesh wall cannot be secretly touched from the outside by a curious individual. 3. Display cages should be designed so that bats can remain somewhat hidden without being totally obscured from view. This may be accomplished with the use of either natura l or artificial materials including fabrics, silk foliage, tree bark, or small tree branches that can be used to simulate natural habitat, depending on the species. These materials should be secured against cage walls and kept clean and free of odors, shar p areas, dirt, and parasites. 4. Areas within the display cage that are in public view where bats have urinated and/or defecated should be inconspicuously cleaned (if possible) with tissue. The tissue should then be put in a plastic bag brought along for tha t purpose, and placed out of sight until after the presentation when it can be disposed of appropriately. EDUCATING CHILDREN While educational programs about bats should attempt to instill a child with a healthy respect for wild animals and their habitats , such a program should begin by emphasizing the importance of never touching a wild animal. A stern message regarding handling of bats and other wild animals should be leveled at children. These messages must be especially emphasized if presenters handle bats during presentations. It is also necessary to be redundant when delivering messages to children. The following examples have proven successful for Bat World*. 1. Children should be told that grownups who handle special training in order to work with wild animals. They should also be told that the bats being used for the presentation are tame and familiar with the handler, whereas bats in the wild are very different and will bite in self defense when handled. 2. Wh en giving the bat a food reward during face and teeth as the bat chews. A cam corder with a modulator hookup will project this image clearly onto a TV screen for si multaneous viewing by the audience. Rat her than hand feeding the bat, food rewards can be placed into the display cage in a way that enables the bat to find and eat the food naturally (e.g., small pieces of apple can be secured onto branches for frugivorous bats; mealworms can be placed in

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 173 shal low dishes camouflaged by leaves or grass for insect eating bats). While the bat eats, explain that a bat uses its teeth to eat food in the wild, but will also use its teeth for protection against predators, including people who may try to touch it. A stro ng visible image can be created while the bat feeds by describing how it uses its teeth for protection. 3. Children should be told that if a bat is found within reach, something must be wrong with it. Remind them to never touch the bat because it might be si ck. Let them know that if they do touch the bat, it will probably bite them and that the bat will need to be killed so that it can be tested for rabies. If the bat has rabies, they will have to have a lot of shots ey. They should be told that touching the bat will prevent them from helping it. Explain that even if they touch the bat and it flies away, they will still have to get shots. Explain that the only way they can help save the bat is to get an adult. If there are other children or domestic pets with them, they should send a friend for an adult so they can stay behind and make sure that other children or pets stay away from the bat until the adult arrives. Finding a bat will probably be both exciting and frustr ating for a child who has learned about that animal. Let them know that they can help the adult who comes by telling him or her to use a can, dustpan, or thick gloves (never bare hands) to scoot the bat into a box that can be covered. If no one had contact with the bat, they can tell the adult to call their state wildlife department, local animal control division, humane society, or wildlife rescue organization for further assistance. 4. Children should be reminded that even though bats are small, they are wi ld animals. They should be told that it is against the law to keep them as pets and, in addition, they would not make good pets anyway because they need special cages, food, temperatures, and sometimes the company of an entire colony of bats, or they will not survive. 5. Relate a story about a child who found a bat, picked it up, was bitten, and had to receive shots. Then ask the children what they would have done differently if they had found the bat. Encourage ouch it, tell an adult, etc.). *Bat World Sanctuary and Educational Center is a licensed facility, and Amanda Lollar is a permitted wildlife rehabilitator. See for more information.

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 174 Bats in the Classroom: A C onceptual Guide for Biology Teachers W.T. Rank in and Norma G. Lewis Duke Rankin is a field biologist with the U.S. Forest Service, Highlands, NC 28741; Norma Lewis is an educator with the Environmental Education Association of Alabama, Huntsville, AL 35084. The American Biology Te acher 64(6): 415 421 T he purpose of this article is to present a group of organisms as an instructional tool for introducing a variety of biological concepts. We find bats particularly useful as a gateway to biological concepts for several reasons. First, bats are among the most widespread mammals in the world, and frequently coexist with human beings. Second, the natural history of bats can be very different from human beings, allowing teachers to compare and contrast evolutionary adaptations to different environments. Third, many people do not understand bat biology, lending an aura of mystery to these animals. Students are frequently fascinated by animals they view as mysterious. As a result, bats may serve as a bridge to biological concepts that may oth erwise be viewed as remote and esoteric. Our goal is to present a list of biological concepts that can be introduced or illustrated using bats as examples. We have used these concepts in both traditional and nontraditional venues, for students from middl e school through college. The concepts include the following: Classification & Phylogeny Bats are the subject of a long running controversy. Traditionally, bats have been placed into a single order, implying a common evolutionary ancestry. Bat biologists argued that complex adaptations such as flight and echolocation could only have evolved once, meaning all bats must have evolved from a common ancestor. Bats can be readily separated, however, into two distinct groups. Microbats enjoy a global distributio n and are the only bats native to the New World. Microbats are typically several inches long (head and body) and have wingspans less than a foot. They have small eyes and the small, sharp teeth characteristic of insectivores. All microbats echolocate, crea ting high pitched sounds in their larynx and using these calls to guide their flight the same way submarines use sonar. Most North American microbats eat insects, but neotropical microbats are just as likely to eat nectar and fruit, and often act as pollin ators for flowers and dispersal agents for seeds. Microbats also tend to roost in caves, trees, and attics. The Old World tropics contain a second group of bats, the megabats. As the name implies, megabats are often larger than microbats: the largest mega bats are 18 inches long (head and body) with wingspans over five feet. Megabats have large eyes and navigate through visual clues. A few species do echolocate, but unlike microbats, megabats echolocate by clicking their tongue against the roof of their mou th. None of the megabats is exclusively insectivorous most eat fruits or nectar. Megabats rarely roost in caves, preferring tree branches. The two groups of bats are so distinct that many bat biologists believe they represent two evolutionary lines. If this is true, it would mean complex adaptations such as bat flight and echolocation evolved twice once in microbats, and once in megabats. It would also suggest the two groups should be placed in separate orders. Speciation One of the current models of speciation is based on the rapid evolution of small, isolated populations. Bats, the only mammals capable of sustained flight, have colonized isolated islands throughout the world bats, for example, are the only mammals native to Hawaii. Bats dispersing across the islands of the Pacific Ocean apparently formed a large number of small, isolated populations that underwent rapid evolution. Many Pacific islands now contain endemic species of bats. Co evolution Co evolution is evolutionary change in one spec ies in response to evolutionary change in a second species. Insectivorous bats locate their prey through echolocation, and insects have evolved adaptations to confuse their predators. Many moths are covered with thick, soft hairs that absorb echolocation s ignals. The signals do not bounce off the moth and the bat is unable to locate the insect. Other insects have ears tuned to the frequencies at which bats echolocate. When these insects hear echolocation, they fold their wings and fall to the ground, emulat ing falling leaves. Still other

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 175 insects attempt to distort signals by producing false signals of their own sonar. A second example of co evolution can be found in bat pollinated flowers. Flowers pollinated by bats exhibit se veral characteristics. For example, most bat pollinated flowers are nocturnal, matching the activity patterns of the bats. The flowers tend to be white or light colored, increasing their visibility at night, and are often characterized by strong, unpleasan t odors. In addition, the flowers are often large and cup shaped the shape may reflect the echolocation calls of microbats, allowing bats to hear the flowers more distinctly than surrounding vegetation. Bats are important pollinators of the saguaro and o rgan pipe cacti of the Sonoran Desert in the American southwest (Figure 1). Physiological Adaptations An adaptation is any trait that increases the survival of an organism. Bats exhibit several distinctive traits that can be interpreted as adaptations for their unique lifestyle. For example, virtually all bats roost upside down; this has profound effects on their physiology. For example, blood flow through a mammal is controlled by valves throughout the circulatory system. If a human being is held upside d own, blood rushes to its head because the valves in the circulatory system are designed to move blood forward when the person stands erect. In comparison to a human being, the circulatory valves of bats are upside down. A bat hanging upside down probably f eels as comfortable as a person standing erect. A second set of physiological adaptations is associated with sanguivory the consumption of blood. Vampire bats are the only mammals exclusively sanguivorous. Blood contains a high concentration of protei ns and is therefore a very nutritious food, but it also poses problems for a small, flying mammal. Blood is mostly water and therefore quite heavy; a vampire who has just consumed a large meal may be too heavy to fly. When a vampire feeds, it produces larg e amounts of very dilute urine, effectively purging the water in its meal. When the bat returns to its roost however, it faces a different problem. Digesting a high protein meal requires a large amount of physiological water to flush urea from the body. Va mpires are small bats that do not contain much water. Although vampire kidneys can produce very dilute urine, they can also be extremely efficient at reclaiming water from urine. As a result, roosting vampires produce one of the most concentrated urines kn own from mammals. Altruistic Behavior Vampires also engage in one of the few examples of altruistic behavior known in mammals. Sanguivory is a difficult procedure, and many vampires are unsuccessful in any given night. When successful vampires return to t heir roost, they will regurgitate blood meals to unsuccessful vampires who are genetically unrelated. Truly altruistic behavior is of special interest to evolutionary biologists because it seems to violate the tenants of natural selection altruistic anim als appear to voluntarily lower their own fitness in comparison to the animals benefiting from the behavior. Morphological Adaptations Bats exhibit a second unique feature associated with roosting. If a human being is hung from a wall by the heels, that p erson would hang with its back to the wall. If a bat is hung from a wall by its heels, the bat is hanging with its stomach to the wall. Beginning at the hip, the legs of a bat are rotated 180°. The knees of a bat face sideways, and the feet face backwards. This is an adaptation for flight. A person hanging from a wall must turn around to flap its arms. A bat, however, merely releases his toes and begins to fly. Figure 1 . The lesser long nosed bat, Leptonycteris curasoae, pollinating a sag uaro flower. Note the close fit between the shape of the flower and the head of the bat. Bat flowers tend to be large, lightly colored, and open at night.

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 176 Flight Bats are the only mammals capable of sustained flight. The wings are formed by two lay ers of skin stretched across the bones of the fingers and attached along the side of the body are translucent: the bones of the hand and the blood vessels supplying the wing can be clearly seen through the skin. Because the blood cells can be viewed medical research to study the effects of drugs on the flow of blood through capillaries. Homology Homology applies to traits shared by species due to descent from a commo n evolutionary ancestor. For example, mammals share the same bone structure in their hands because they evolved from a common ancestor with those characteristics. Despite dramatic modifications towards different purposes, bat hands have the same bones as h uman hands (Figure 2). This can be readily demonstrated in class using photographs of flying bats. Echolocation Echolocation is a form of sonar: the bat emits high frequency sounds that bounce off objects and return to the bat. Bats use these high freque ncy echoes to find prey and navigate through caves and forests. Bats that echolocate often have disproportionately large ears the ears of the spotted bat, for example, are two thirds as navigate in complete darkness. Echolocation appears to be primarily a means of foraging. Echolocation is most characteristic of bats that hunt flying insects; many bats that eat fruit do not echolocate. The most sensitive echolocation, however, belongs to the fish ing bat of Central America. It can detect the dorsal fin of a fish only a few millimeters above the surface of the water. The bat flies over the water and locates a fish when it breaks the surface. Using the long claws on its feet, the bat then scoops the fish out of the water and eats it (see page 417). Human Biology Because they frequently share the same habitat, bats and Figure 2. The frog eating bat, Trachops cirrhosus, attacking an unsuspecting frog. The fingers on t he hand are evident in the wing, beginning with the claw like thumb, the short index finger at the leading edge of the wing, the middle finger extending to the tip of the wing, and the third and fourth fingers forming the points along the trailing edge of the wing. evident midway between the palm and body. The knee is also evident, flexed in the plane of the wing. And, unlike human beings, the soles of the feet hand downward, facing the ventral surfa ce of the bat.

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 177 people have enjoyed a long and colorful history. People have surrounded bats with myths (see Sidebar), conscripted them into the mili tary, and boiled them in coconut milk for dinner. The most common interaction between bats and people is pest management. Several species of North American bats will roost in buildings. The attics of buildings often provide ideal conditions for bats: atti cs are dark, dry, and offer a variety of temperatures. Most bat problems occur in the fall, when young bats explore inappropriate habitats, and the winter, when hibernating bats may seek warmer environments. Bats can be readily excluded from attics using s imple exclusion devices that allow bats to leave the attic, but prevent bats from returning. Before attempting an exclusion, however, please contact an experienced bat person or organization improper exclusion can expose people to unnecessary health risk s. Bat problems can provide excellent learning opportunities. Mary Engles, a biology teacher at Vincent High School (Vincent, Alabama), found herself in the midst of a bat problem when bats began flying through the halls of the school. Mary was forced to a nswer questions about the presence of the bats, the safety of the students, and the management options for excluding students researched and built bat houses to provide alternative roosting sites. We have found bat house construction to be a useful, hands on activity that allows students to take a personal involvement in bats. Our goal

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 178 has been to illustrate some of the possibilities associated with the use of bats as a teaching tool. Additional informatio n on bat biology is available from several organizations specializing in bat education (Table 1). Several organizations offer workshops on bat biology, which are designed for both teachers and conservation professionals for example, Bat Conservation Inte rnational leads week long workshops in several locations each summer. Perhaps the best opportunity for classroom teachers, however, are weekend workshops offered by the Lubee Foundation in Gainesville, Flor ida ( ). Acknowledgments We thank Dr. Scott Peterson, John Seyjagat, and Janet Tyburec for their comments on early drafts of the manuscript. We also thank Merlin Tuttle, retired Founder and Executive Director of Bat Conservation International, for donating the photographs used to illustrat e this paper.

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 179 Rabies by Amanda Lollar and Barbara Schmidt French Reprinted with permission from: Captive Care and Medical Reference for the Rehabilitation of Insectivorous Bats , 1998. Bat World Publications, Mineral Wells, TX. 3 29 pages. HUMAN EXPOSURE Rabies is a viral infection of the central nervous system resulting in fatal inflammation of the brain and sometimes, the spinal cord as well. Despite the fact that more than 30,000 humans die from rabies each year worldwide, ver y few of these deaths can be attributed to rabies of insectivorous bat origin. Since 1953, only a few dozen cases of human deaths due to rabies have been attributed to insectivorous bats, 35 of these having been documented in the United States as of Decemb er 31, 1998. Although the majority of these cases were formerly attributed to a variant of virus believed to be associated with the silver haired bat ( Lasionycteris noctivagans ), many of these cases are now being attributed to a variant believed to be asso ciated with the eastern pipistrelle ( Pipistrellus subflavus ). Researchers are trying to unravel what role these bats play in the epidemiology of human exposure. Although modern technology allows for the identification of the specific variant of the virus, it identifies only the original host; it does not provide identification of any possible intermediate hosts such as terrestrial mammals or other bat species. Exposure to rabies virus typically results from bites of an infected animal. Less common modes of exposure include direct contact of open wounds, cuts, or abrasions with saliva or nervous tissue of an infected animal, contact of mucous membranes (e.g., eyes, nose, mouth) with infected saliva or nervous tissue, and inhalation of aerosolized virus. Alth ough some of the recent human cases attributed to bat variants of the virus report no evidence of a bat bite, it is not possible to eliminate a bite as the mode of exposure. In some cases, the individuals were known to have actually handled bats or there w as a report of a bat having been onset of clinical signs of disease. In addition, by the time the disease was diagnosed, some victims had already died or were too ill to provide specifics regarding the ki nd of contact they had or may have had with a bat or other wild animal. In such cases, medical professionals were forced to rely on whatever information could be provided by family members or friends. Although the authors have found that bat bites are cert ainly felt, they do not always leave readily detectable marks on the skin. While victims of bites from terrestrial mammals such as raccoons are likely to seek medical treatment, this may not be the case with victims of bat bites. Unfortunately, the lack of a visible bite mark may have led some victims to dismiss such an encounter as insignificant. Denny Constantine, formerly with the California Department of Health Services in Berkeley, California, studied rabies in bats extensively. According to Constanti 1953 as a consequence of increasing awareness of the problem . . .The infected bats were among many thousands of bats submitted for testing, usually because the bats, either disabled or dead, had been captu red by pets or children, and bites were known or suspected to have occurred. About ten percent of the bats submitted in this manner for testing in the United States prove to be infected, a proportion that has not changed over the years. It should be emphas ized that these bats represent a highly biased sample, because nearly all of them were ill or dead department statistics can vary significantly from those of wild bat populations and why comparisons of w ild to suspect submission rabies prevalence is of limited value. No survey methods are likely to be entirely unbiased. Because sick bats are more easily caught than healthy ones, surveys taken in roosts may overestimate the frequency of infection in the p opulation in general. Daytime surveys of night roosts may contain only incapacitated individuals (i.e., those unable to return to daytime retreats). Constantine indicates that such surveys may lead to mistaken impressions of rabies outbreaks, but . . nothing resembling an outbreak or large scale rabies destruction of a bat colony has been detected, are of bats capable of flight, suc h as bats issuing from cave entrances. From such sampling, it has been learned that only a small proportion (<0.1 to 0.5 percent) may be issuing from cave entrances would not include bats that are clinically ill and no longer able to fly, they would include infectious bats in pre clinical stages.

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 180 Despite low rates of infection in wild populations, there is likely to be a much higher frequency of infection in the sick and injured population rehabili tators treat. They handle a highly suspect population similar to the population many health departments receive for testing. For example, 72 bats received at the French rehabilitation facility that either died or that were euthanized between 5/16/96 and 6/ 27/98 were tested for rabies in a collaborative study with Charles Trimarchi, DVM, of the New York State Department of Health. One bat was untestable due to physical trauma. Of the remaining 71 bats, six (approximately 8%) tested positive for rabies. (Perc entages varied from one species to another, ranging from 0% to 19%.) This emphasizes the importance of pre exposure immunization for bat handlers. According to the U.S. Centers for Disease Control and Prevention (CDC), post exposure prophylaxis is indicat ed following a bite or scratch from a confirmed rabid bat or from one that is not available (or suitable) for testing. The authors have found that some people are reluctant to admit to such encounters. Although this is sometimes due to a concern for the we lfare of testing), more often it is due to a reluctance to admit to inappropriate behavior (i.e., catching or otherwise handling a wild animal). This may be particularly true of children. It is, theref ore, important that rehabilitators carefully inform persons turning bats over to them of the potential consequences of untreated exposure to an infected animal. The CDC recommends that a bat be tested for rabies if it is found in a room with a person who c annot be considered an accurate historian (i.e, a person who may not be able or willing to give accurate information about potential contact with the bat such as a child, or a mentally disable, sleeping, or intoxicated person). Concern has frequently been voiced about the potential threat of aerosolized rabies virus. Brass (1994) summarizes instances in which rabies have occurred in humans and animals as a result of inhalation of aerosolized virus. Only two human cases of aerosol transmission of bat rabies have been suspected, both in the 1950's. Brass (1996) suggests that misquotes, misunderstandings, and information carried out of appropriate context have resulted in reports that are misleading about this issue. In truth, aerosol transmission is suspected only within the unique conditions that exist in a small number of caves in the Southwest that house large nursery colonies of Mexican free tailed bats ( Tadarida brasiliensis ). Rabies virus has been isolated from the air of such caves and sentinel animals placed in them have developed rabies without direct contact with bats. The unique atmospheric conditions resulting in caves housing these large maternity colonies (i.e., the presence of hundreds of bats combined with poor ventilation) may have played a con tributory role in aerosolized transmission of rabies (Constantine, 1967). Viral entry points could have included skin wounds, the alimentary tract or respiratory mucosa. Brass (1996) points out that aerosolized virus was not detected in subsequent studies of caves housing large bat colonies in Oklahoma, Alabama, and Tennessee, and that rabies researchers do not believe that caves in the northern temperate zone are conducive to airborne transmission. Neither are such conditions found in buildings housing typ ical bat colonies. Brass (1994) discusses this issue at length, providing specifics about each of the human cases. In so doing, he states that the evidence that the two deaths in the 1950's resulted from inhalation of aerosolized virus remains questionabl e. In particular, one victim, an entomologist with the Texas State Health Department who died in 1956, reported no bites but was known to have actually handled thousands of bats as a member of a rabies investigative team. An area of chronic skin irritation might also have had a contributory role in this particular case. The second victim, a consultant mining engineer who died in 1959, reported no bite although one report indicated he had been These facts led Brass to conclude that the risk of inhalation exposure to cavers exploring caves other than the aforementioned nursery colonies in the Southwest is not be of even remote concern to either the general public or the va st majority of the caving community, since it is a phenomenon known only from the research laboratory and possibly the exploration of certain unique underground Brass (1994) also notes that there has been no report of bat infl icted rabies in a caver secondary to a bite sustained while underground despite the hundreds of thousands of man hours spend underground annually by members of the National Speleological Society. Nonetheless, the author does note the possibility of direct contact with bats during cave exploration despite the fact that conscientious cavers try to avoid disturbing bats. He empathizes prevention and

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 181 possible protection derives from common sense caution in handling bats and from prompt wound care and post exposure rabies prophylaxis in the unlikely eventuality that a bite from a rabies bat (or from one Only laboratory testing of brain tissue can positive ly identify rabies infection in bats . Rabies infection cannot reliably be excluded by antemortem testing (i.e., testing of a live animal for rabies). This is to say, a positive diagnosis of rabies testing in a living animal is conclusive, but a negative te st is not. As previously indicated in this manual, bats that have human contact should always be submitted to animal control or local health departments who will determine if rabies testing is warranted. BAT BITES Bites or scratches from the claws of Nort h American bats may or may not leave marks on the skin. All bats are capable of inflicting bites that leave marks despite the fact that they may not always do so. Visible bite marks can range from simple indentations in the epidermis that disappear within moments, to tiny scratches (that can occur when a bat jerks its head while biting), to deeper puncture marks that may or may not result in bleeding. Bites from species found in the United States and Canada are frequently visible as two to four tiny punctur e marks, often spaced about 4mm to 5mm apart, depending on the species. The punctures are caused by the canines, either the upper and lower canines on one side of the jaw leaving two puncture marks, or the upper and lower canines of both sides of the jaw l eaving as many as four puncture marks. Bites are commonly received on the fingers or hand by people who handle or otherwise touch a bat. Bites can also result on various parts of the body when a person brushes against or has other bodily contact with a ba presence. For example, a bite could occur if an individual sat on a chair that a grounded bat had crawled onto. Marks generally fade quickly and are frequently no longer visible after only one or two days. Some bit es may be visible for a longer period of time, although seldom more than a week or two. Bites that actually puncture the skin can be painful when received (a sensation similar to that experienced from a needle jab). Because bats do not always release thei r bite immediately, they must sometimes be encouraged to do so. Attempting to pry their teeth apart with a pencil or other object is inappropriate (and time consuming). Blowing in the face of the bat will often cause it to release its hold. When all else f ails, make one quick flick of the wrist while the hand is open and held above a soft surface. This action startles the bat, causing it to release its hold. CLINICAL SIGNS OF RABIES IN INSEC TIVOROUS BATS The incubation period is the interval between expos ure to viral infection and the appearance of the first clinical sign of disease. An incubation period of at least 209 days was reported in a naturally infected big brown bat (Moore and Raymond, 1970 [cited by Brass, 1994]). There are also reports of incuba tion periods of over one year (Kaplan, 1969 [cited by Brass, 1994]; Trimarchi, 1978 [cited by Brass, 1994]). Although the authors have observed a number of clinical signs in bats testing positive for rabies, lack of observable clinical signs of disease ca nnot be used as a basis for determining if a bat is or is not infected with the rabies virus . Even clinically normal bats are of unknown infection status. Although the authors have found that bats infected with rabies frequently die within a few days (ofte n within 24 to 48 hours) after being obtained by a rehabilitator, the maximum period of viral shedding (the period of time during which the virus is present in the saliva and the disease can be transmitted to others) prior to the onset of clinical signs in bats (and most other wild animals) is unknown. Virus has been detected in bat saliva as much as 12 days prior to the onset of clinical signs of disease (Baer and Bales, 1967; Baer, 1975; Constantine, 1998). Therefore, even bats that appear to be healthy c ould be shedding virus and thus be capable of transmitting it to people or other animals. Clinical signs of rabies infection in Mexican free tailed bats ( T. brasiliensis ) documented by Constantine (1967) are predominantly paralytic rather than furious in nature. Irritability or depression, weakness, anorexia, hypothermia, and paralysis may characterize the disease in this species. Clinically ill individuals sometimes flap their wings and squeak loudly when people approach, although they are unlikely to att ack observers. They do sometimes bite at objects near them, but generally appear focused on their own debilitated state. Squeaking and buzzing have also been reported by other researchers (Centers for Disease Control, 1954 [cited by Brass, 1994]; Bell et. al., 1955 [cited by Brass, 1994]; Moore and Raymond, 1970

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 182 [cited by Brass, 1994]; Schowalter, 1980 [cited by Brass, 1994]; Haagsma, 1989 [cited by Brass, 1994]). These bats may be dehydrated, emaciated, hypothermic, and are often found roosting alone (Sull ivan et. al., 1954 [cited by Brass, 1994]; Constantine, 1988). They are sometimes observed flying during the daytime and may collide with objects (Bell et. al., 1957 [cited by Brass, 1994]; Constantien, 1967; Price and Evard, 1977 [cited by Brass, 1994]). However, some species of bats normally fly in the late afternoon. Healthy bats will also fly out of roosts during the day if sufficiently disturbed. The authors often observe aggressive biting and incessant chewing by rabid bats on items that come into co ntact with them, including inanimate objects such as caging materials. Incessant chewing on inanimate objects in particular is not typical of healthy bats, with the exception of mating males of some species, such as T. brasiliensis , in captive colonies. Th ese males do sometimes exhibit aggression towards intruders (i.e., handlers or bats, males or females, that enter their territories Lollar, 1994). Rabid bats often do not show an interest in exploring or moving around within their environment. Rather, th ese animals often seem to prefer to remain exposed in one spot with eyes closed or half closed, only responding when anything approaches them. They do not seem to aggressively seek out objects or other animals, but rather bite at whatever materials (or peo ple) that happen to touch them. Verified reports of unprovoked bat attacks are exceedingly rare. The authors individuals who are surprised by a bat that inadvertently flies into their home through an open door or over their head at a porch light. These people can be quite insistent that the bat in question is attempting to attack them until rescue personnel arrive on the scene and give them the opportunity to see that although the bat will continue to fly around the room, it does not actually jump onto or attack the rescuer. They often express surprise at this observation. French has also observed sick or injured foliage roosting species, such as red bats ( Lasiurus borealis ), spread their wings and release their grip from their roost when startled. Because they are too weak to fly, they subsequently flutter to the ground. It is understandable that a rare encounter with such a bat would be mistaken for an attack. The authors have found that, while not alway s a reliable indication of rabies infection, uninjured crevice dwelling bats with rabies are often found in exposed areas during daylight. Do not assume that injury precludes rabies infection, however. In fact, rabid bats may sustain injury once they have become sick enough to be grounded. On the other hand, illness and injury does not necessarily mean rabies. Any injured bat that has become grounded may squeak and flap its wings in an attempt to escape capture. However, the authors have also observed cont inuous wing flapping and repeated vocalization in rabid bats. We have also observed the following neurological signs including uncoordinated movements, spastic paralysis of the hind legs, seizures, a hunched back, and legs clamped up against the abdomen in bats testing positive for rabies (although similar signs may also accompany other conditions including pesticide poisoning and back injuries Lollar, 1994; Clark, et al., 1996). We have also found that the presence of dirt and/or other foreign substance another indication of rabies infection, possibly resulting when an infected animal bites at the ground or other surroundings. In addition, rabid bats may refuse to eat or drink and become dehydrated. However, rehabilitat ors should not consider dehydration in itself as being diagnostic of rabies, since many unrelated conditions may also lead to dehydration. Alternatively, we have found that although it is not common, some rabid bats will readily accept both food and water. Rabies infected bats may also exhibit signs of respiratory distress. French observed bleeding from the ears and mouth of one rabid bat that appeared unable to move its head and neck. Although observation of signs in a single bat have no statistical signi ficance, we feel it is important for rehabilitators to be aware of all of the signs we have observed in bats that have tested positive for rabies. This bat had no other obvious injuries. It is possible that bleeding could have been associated with a head o r other injury sustained as the result of a crash or fall due to weakness or the kind of erratic flight that often characterizes rabies in bats. Bleeding from the ears, nose, or mouth may also be associated with pesticide poisoning (Clark, et al., 1996) an d heat stroke. Rabies is a fatal disease for people as well as bats. Rehabbers should protect themselves and humanely euthanize bats demonstrating signs of rabies infection. In case of an animal bite and/or scratch or contact with saliva or nervous tissue from a suspect animal, consult your

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 183 family physician immediately. Animals involved in such instances must be turned over to authorities for rabies testing. (Care should be taken to prevent physical damage to the brain of an animal that must be tested for rabies.) If you do not have access to a physician, contact your local or state health department. These officials will direct you to the proper emergency medical professionals in your area who have access to the required vaccine. If local or state health d epartment personnel are unavailable, call the Viral and Rickettsial Diseases Division of the U.S. Centers for Disease Control and Prevention at (404) 639 1075 weekdays, or at (404) 639 2888 nights, weekends, or holidays. There has been little research in the area of rabies vaccination for bats, as vaccination of large, wild populations may not be a feasible undertaking. However, Charles Trimarchi, DVM, with the New most health agencies neither endorse no r prohibit extra label use of rabies vaccines in wildlife, modern vaccines may protect wild species and because they are killed virus vaccines, do not pose a risk of vaccine French and Lollar vaccinate bats ta ken in from the wild that will be added to captive study colonies in order to minimize the potential of disease transmission to other captives. These bats are vaccinated annually with the Imrab 3 rabies vaccine. Each bat is injected subcutaneously with 0.0 5ml. However, Trimarchi notes otherwise potentially exposed a human or domestic animal, the vaccination will not be recognized as pertinent by health agencies; (ii) if the animal is in contact with a kn own rabid animal, it will still have to be confined for six months or euthanized; (iii) if the animal develops CNS (Trimarchi, 1996). It is also important to note that a negative test on one captive ba t in a cage does not necessarily reflect the rabies status of another bat housed in the same cage. Human rabies cases in the United States believed to be associated with the following bat species, or viral variants: Scientific Name Common Name Incidence Pipistrellus subflavus Eastern pipistrelle 15 Lasionycteris noctivagans Silver haired bat 8 Tadarida brasiliensis Mexican free tailed bat 5 Eptesicus fuscus Big brown bat 2 Myotis species Plain nosed bat species 2 REFERENCES : Baer, G.M. (1975). Rab ies in nonhematophagous bats. The Natural History of Rabies . Academic Press. New York. Baer, G.M., and G.L. Bales (1967). Experimental rabies infection in the Mexican freetail bat. Journal of Infectious Diseases . 117:82. Bell, J.F., W.J. Hadlow, and W.L. J ellison (1955). Chiropteran rabies in Montana. Public Health Reports . 70(10): 991. Bell, J.F., W.J. Hadlow, and W.L. Jellison (1957). A survey of chiropteran rabies in western Montana. Public Health Reports . 72(1): 16. Brass, D.A. (1994). Rabies in Bats: N atural History and Public Health Implications . Livia press. Ridgefield, Connecticut. Brass, D.A. (1996). Human rabies of insectivorous bat origin, 1994 1995. NSS News . 54(9): 42 246. Centers for Disease Control (1954). Midwestern CDC Services. Report from the Rocky Mountain Laboratory . Hamilton, Montana. Clark, D.R., A. Lollar, and D.F. Cowman (1996). Dead and dying Brazilian free tailed bats ( Tadarida brasiliensis ) from Texas: Rabies and pesticide exposure. The Southwestern Naturalist . 41: 275 278. Consta ntine, D.G. (1967). Bat rabies in the southwestern United States. Public Health Reports . 82(10): 867. Constantine, D.G. (1988). Health precautions for bat researchers. In T.H. Kunz (ed.), Ecological and Behavioral Methods for the Study of Bats . Smithsonian Institution Press. Washington, D.C. Haagsma, J. (1989). Rabies en vleermuizen: how te handelen? Ned. Tijdschr. Geneeskd . 133(11): 550. Kaplan, M.M. (1969). Epidemiology of rabies. Nature . 221(5179): 421. Lollar, A.L. (1994). Rehabilitation and Captive Car e for the Mexican Free tailed Bat . Bat World. Mineral Wells, Texas. Moore, G.J., and G.H. Raymond (1970). Prolonged incubation period of rabies in a natural infected insectivorous bat, Eptesicus fuscus (Beavios). Journal of Wildlife Diseases . 6: 167. Price , J.L., and C.O.R. Everard (1977). Rabies virus and antibody in bats in Grenada and Trinidad. Journal of Wildlife Diseases . 13: 131. Trimarchi, C. (1978). Rabies in insectivorous temperate zone bats. Bat Research News . 19(1): 7.

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 184 Bats and the Public: On li ne, Up to the minute Resources on the BCI Website Kids and Education: Bat Curriculum Publications, curricula and tools to help teachers bring bats to the classroom. Educators Navigation Page Links that help bsite. Kidz Cave Fun filled activities, games and info Meet Our Flying Foxes! These lovable flying Photos BCI Photo Library Browse our collection of bat photos and order your favorites. Desktop Wallpaper Pick a bat photo to liven up your computer screen. Photographing Bats Tips from the master: BCI Founder, Merlin D. Tuttle. Articles and Information Audio/Visual Programs Download or order videos and PowerPoin t presentations that show the incredible diversity and value of bats. BATS Magazine filled member magazine dating back to the 1980s. Informational Flyers Learn what you should know about bats from these free downloads. Latest News Job openings, volunteer opportunities, conference schedules and lots of news. Natura l History of Bats The basic facts about flying mammals that have been around for 50 million years. Species Profiles Portraits, information, and ranges fo r each bat species in North America. Bats and the Public Bats in Buildings What do you do when you find a bat in your house or building? Exclusion guidelines, fact sheets, and a bat removal video. FAQs Answers to frequently asked questions about bats, bat houses, and public health. Find Bat Locations Bracken Cave owned cave near San Antonio. Congress Avenue Bridge 1.5 million bats emerge each summer evening in the middle of downtown. Other sites in Texa s Find out where to go to view spectacular bat flights throughout Texas. Workshops Complete on line directory to all BCI sponsored workshops; including Bat Conservation and Management, Acoustic Monitoring, Cave Gating and more.

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 185 Use of Artificial Roo sts by Forest Dwelling Bats in Northern Arizona By Carol L. Chambers, Victor Alm, Melissa S. Siders, and Michael J. Rabe Wildlife Society Bulletin 30(4): 1 7 , 2002 Forest dwelling bats often use snags and live trees as maternity and bachelor roost sites. T hese roost sites can be destroyed or altered by natural events (e.g., wildfire) or forest management activities (e.g., prescribed fire, thinning, harvesting). To determine whether artificial roost structures could supplement natural roost sites, we tested 2 types of artificial structures for use by bats: resin ( n =10) and wood ( n =10) roosts. Artificial roosts were placed on snags in 6 ponderosa pine ( Pinus ponderosa ) stands and compared with use of nearby natural roost snags ( n =10). We monitored the 3 roost types (resin, wood, natural) approximately every 2 weeks for use by bats for 2 summers (1999 and 2000). Over the 2 yr period, bats used 17 of 20 artificial roosts (8 resin and 9 wood), using both artificial roost types in about equal proportions. Bats used 5 of the 10 natural snags monitored. Resin roosts were camouflaged to match tree bark, have a >20 year lifespan, and cost US $42 each after construction of a $250 mold. They can be resigned to resemble any tree species. Wood roosts cost about $5 each, wer e more visible, and likely have a shorter lifespan than resin roosts. Both roost types might require some annual maintenance (recaulking tops and edges). Maintaining and managing for natural roosts should be a priority for resource managers since artificia l roosts might not provide the same microclimate as natural roosts. However, artificial roosts might be useful temporary habitat under site specific conditions. Artificial roosts could also be useful as research tools. Key words : Arizona, artificial roost s, bats, fire, Pinus ponderosa , ponderosa pine, roost habitat, snags, Southwest Many forest dwelling bats in ponderosa pine ( Pinus ponderosa ) ecosystems (e.g., long eared myotis [ Myotis evotis ] , fringed myotis [ Myotis thysanodes ] , long legged myotis [ Myo tis volans browed bat [ Idionycteris phyllotis ] , and big brown bat [ Eptesicus fuscus ]) rely on large (>69 cm diameter at breast height [dbh]) ponderosa pine snags as primary roost sites (Rabe et al. 1998, Barclay and Brigham 2001). Roosts o ften are located under large pieces of loose, exfoliating bark that provide insulation and allow bats to move during the day to seek optimum temperatures. Because of their reliance on large snags, forest bat populations are likely sensitive to roost site d estruction. Forest management treatments (e.g., thinning, prescribed burning) are being implemented in response to the increased threat of wildfire in the southwestern United States (Covington et al. 1997, Swetnam et al. 1999). However, these management t reatments might reduce the availability of snags. Thinning might inadvertently remove snags, and prescribed fire or wildfire might incinerate or alter snags (Horton and Mannan 1988, Dwyer and Block 2000, Randall Parker and Miller 2002) that serve as roost sites for bats. Although prescribed fire or wildfire also creates snags (Gaines et al. 1958, Boucher et al. 1999), live trees killed by fire generally are small in diameter and therefore not effective replacements of large snags selected by bats, nor do th ey have exfoliating bark that is used by bats for roost sites (Rabe et al. 1998). Horton and Mannan (1988) found that large (>30 cm dbh) and more decayed ponderosa pine snags were more flammable, therefore more likely to be lost to fire. This loss of large dead wood might be particularly detrimental to bats, since bats select larger snags (>69 cm diameter) and replacement of large snags could take a long time (e.g., >200 years for a ponderosa pine to reach 50 cm dbh under normal stocking, site index 70 [Mey er 1961]). In situations where roosts snags are altered or removed, artificial bat roosts might enhance or maintain bat roost habitat (Fenton 1997). In Thetford Forest, England, the population of brown long eared bats ( Plecotus auritus) doubled after 10 years when artificial bat boxes were added. Population increase was attributed to recruitment rather than immigration, suggesting that roost sites had been limiting (Boyd and Stebbings 1989). Other successful uses of box type artificial roosts have been do cumented in Europe (Luger 1977, Ziegler and Ziegler 1991). To test the value of artificial roosts in ponderosa pine forests of northern Arizona, we studied the effectiveness of 2 designs. The first roost was made of a polyester resin shaped and painted to resemble exfoliating bark found on ponderosa pine snags. The second type was hand constructed of tempered hardboard (wood) that served as a less expensive alternative to the first design. Our objectives were to determine whether 1) forest bats

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 186 would use artificial roosts and 2) forest bats selected between artificial roost types. Study area We placed artificial bat roosts in 6 16 ha stands in the Fort Valley Experimental Forest located northwest of Flagstaff, Arizona (Township 22N,Range 6E, Section 24 ; Township 22N, Range 7E, Sections 19 and 29, Gila and Salt River Meridian) (P. Fulé,T. Heinlein, and A. Waltz, Northern Arizona University, unpublished report). We selected 3 unharvested stands and 3 treated ponderosa pine stands for roost placement. In u nharvested stands ponderosa pine averaged 1,201 trees/ha; in treated stands trees had been thinned to 172/ha. Trees were <80 cm diameter in all stands (P. Fulé, T. Heinlein, and A. Waltz, Northern Arizona University, unpublished report). Treated stands wer e thinned in 1999 prior to artificial roost attachment, and burned in 2000 after roosts were introduced. Prior to thinning, all stands were similar in ponderosa pine density. Methods We used 2 types of artificial bat roosts: 1) wood roosts made of temper ed hardboard (which had 1 smooth and 1 rough side and was specially treated to create extra water resistance, surface hardness, rigidity, bending, and tensile strength [Phillips Ply wood Company, Inc. 2002]; we used the rough sur face as the interior of th e roost [Figure 1 a ]), and 2) polyester resin molds shaped and painted to resem ble exfoliating bark found on ponderosa pine snags (Figure 1b). We constructed wood roosts from a 0.6 × 0.6 m piece of 0.3 cm thick tempered hardboard and wooden wedges fabric ated from 5 × 10 cm pine lumber. The wooden wedges, which hold the hard board away from the snag, could be made to any size. We cut wedges so that openings at the bottom of roosts were approximately 5 cm wide to allow bats easy access. We attached wedges t o hardboard with weather resistant, self tapping (pointed, with self cutting threads) deck screws and finish wash ers (beveled to countersink the screw head). Holes were predrilled in each roost for ease of attachment to snags in the field. Wood roosts (Fi gure 2 a ) cost US <$5 each, making them an inexpensive alterna tive to resin roosts. Resin roosts were made of flexible isothalic poly ester resin and reinforced with fiberglass mat, man ufactured by Wesco Enterprises (Rancho Cordova, Calif.). They were 1 00% ultraviolet stable. We inserted 3 decay resistant (e.g., redwood, Sequoia sempervirens ) wood partitions inside each roost to increase the number of roost sites for bats (Figure 1 c ). Resin roosts cost $42 each with an initial $250 charge to create the r ubber mold (Figure 2 b ). Both resin and wood roosts could be attached to snags

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 187 of varying size (from 46 90 cm dbh for our study). Both artificial roost types measured 0.6 × 0.6 m and were secured to snags with 3 15 cm deck screws across the top of the art ificial roost and 2 down each side. We used grommets between screw heads and the artificial roost to prevent dam aging the roost. We used brown caulk to seal the top and sides to prevent moisture from entering the roost, and left the bottom open for access by bats. In 4 (2 unharvested, 2 treated) of the 6 stands, we selected 2 groups of snags in each stand to serve as substrates for artificial roosts and as areas to check for natural roosts (controls). In each of the remaining 2 stands (1 unharvested, 1 treated) we selected only 1 group of snags per stand because few of the snags present were of adequate size . Each snag group consisted of 3 ponderosa pine snags that were >31 cm dbh and <75 m apart. From each group we randomly chose 1 snag for attachment of a resin roost and 1 for a wood roost; 1 was left as a natural (control) roost (exfoliating bark present). We attached artificial roosts (resin or wood) to the trunk 2 4 m above the ground. Aspect of roost attachment was constrained by available attach m ent sites on each snag. We made no attempt to randomize roost aspect. Ten roosts of each of the 3 types were placed (artificial) or chosen (natural) for a total of 30 roosts in 6 stands. We left roosts in place for the duration of the study and sampled the same roosts each year, except for 1 control snag that fell and 1 snag and its wood roost that were destroyed by a prescribed burn. We did not monitor the 2 destroyed roosts after 1999. We monitored all roosts for use by bats 3 4 times (approx. every 2 we eks) between 19 July and 26 August 1999 (Year 1) and 10 July and 8 August 2000 (Year 2). We determined use of roosts by the presence or absence of guano ( n >1 pellet; x =96 pellets per roost, range = 1 1,700 pellets) found in wire mesh catch nets attached to the snag approximately 0.6 m below the roosts (Figures 2 a and b ). We monitored natural snags by attaching netting around the base of each. We did not infer abundance, density, or species of bats from guano deposits; however, if bats were present in roo sts, (visual or aural confirmation), we identified them to species when possible. We selected large diameter snags based on prior observations of bat use in the area (Rabe et al. 1998). For each snag, we recorded height, dbh, and decay class (adapted fro m Maser et al. 1979). Snags averaged 63.5 cm (SE=2.5 cm) dbh. Snags were in decay classes 3 ( n =5), 4 ( n =4), and 6 ( n =21;Table 1). We compared use among roost types by pooling data from both years. We compared the observed proportion of use to a 95% confide nce interval of expected use (chi square goodness of fit test, Sokal and Rohlf 1981). Since proportions of available roost types were equivalent, 1 confidence interval was sufficient to compare use of the 3 roost types. Results In 1999 bats used 15 of 2 0 artificial roosts (8 wood and 7 resin) and roosted in 5 of 10 control snags. Ten artificial roosts (5 wood, 5 resin) were in thinned stands and 5 (3 wood, 2 resin) were in unthinned stands. Four of the control snags used were in thinned stands; 1 was in an unthinned stand. In 2000 bats used 14 of 19 artificial roosts (7 wood and

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 188 7 resin; prescribed fire destroyed 1 wood roost) and 3 of 9 control snags (1 had fallen). Nine artificial roosts (4 wood, 5 resin) were in thinned stands, and 5 (3 wood, 2 resin) were in unthinned stands. Two of the control snags used were in thinned stands; 1 was in an unthinned stand. With years pooled, 17 artificial roosts (9 wood and 8 resin) were used by bats and 5 control snags were used. We did not detect a difference bet ween observed use of t Ten artificial roosts (5 wood, 5 resin) were in thinned stands and 7 (4 wood, 3 resin) were in unthinned stands. Four of the con trol snags used were in thinned stands; 1 was in an unthinned stand. Discussion Artificial roost use -Roosts provide bats with cover and concealment from predators and a protected microclimate (Jones et al. 1995, Palmeirim and Rodrigues 1995, Vonhoff and Barclay 1996). Bats in many forest ecosystems select snags for use as roosts (Barclay and Brigham 1996, Rabe et al. 1998, Lacki and Schwierjohann 2001). However, snags are ephemeral and subject to loss through attrition or from forest management practices. Both types of artificial roosts (resin and wood) used in this stud y were effective as roost sites for some forest dwelling bats. We noted use of roosts (natural and artificial) in thinned stands ( n =14) and unthinned stands ( n = 8), but because of small sample sizes we did not test for differences in use of stand type . If bats selected more open forest conditions, this might have been because of increased availability of foraging and commuting areas (Grindal and Brigham 1998) and flight, navigational, and evasive space (e.g., to avoid aerial predators; Vonhoff and Barc lay 1996). How ever, forest dwelling bats also might select habitat based on tree density, and dense forest conditions might be important for some species. In our study, at least 2 species used artificial roosts. We found 2 big brown bats (1 a nonrepro du ctive female; the other evaded capture) in a wood roost in August 2000. In July 2001, we found a maternity colony of long eared myotis (>7 bats including 3 juveniles and 4 adults) in a resin roost. We suspect other species also used our roosts; how ever, w e could not identify bat species from guano samples, and we did not want to disturb roosting bats during the study period. We installed artificial resin roosts in 2 other loca tions in northern Arizona prior to our study. We installed them where bats wer e known to be pres ent but roost habitat was thought to be limiting (i.e., loss of large snags and lack of replacements for snags). We monitored these artificial roosts only periodically, but bats used artificial roosts at both locations: 1) On the Coconin o National Forest in ponderosa pine Gambel oak ( Quercus gambelii browed bats used 2 artificial resin roosts (M. J. Rabe, Arizona Game and Fish Department, unpublished data). We found an browed bat roost under b ark on a ponderosa pine snag in 1994; bats also used this roost in browed bats in the resin roost the next two summers, and they also used another resin roost in the same area. 2) We paced resin roosts ( n = 67) on live pond erosa pine trees (>60 cm dbh) on the Kaibab Plateau beginning in 1997 in open forest patches (M.S. Siders, North Kaibab Ranger Station, unpublished data). In 1997, 33% of roosts were

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 189 used, 90% were used in 1998, 45% in 1999, and 61% in 2000 (all determinat ions of roost use were based on presence of guano; M.S. Siders, North Kaibab Ranger Station, unpublished data). These data indicated that bats were able to locate and use roosts on both snags and live trees. Artificial roosts might help supplement natural habitat in areas where natural snags have not yet formed suitable roosting structures (loose batk) or replacement snags of adequate size are lacking (e.g., through natural attrition or destruction by natural disturbances such as wildfire), altered or remo ved (through forest management activities). However, artificial roosts might not effectively replace natural snags. Natural snags might offer different microclimates or roosting substrates, or provide other functions that artificial roosts do not provide. Of the 20 artificial roosts we monitored in this study, bats used 15 in 1999 and 14 in 2000. Bats did not appear to select one type of artificial roost over another (both resin and wood roosts were used in about equap proportion), although this might be a ttributable to small sample sizes or a limited number of natural roosts in these areas. Both resin and wood roosts were purposely designed to attract bats. Comparison of artificial roosts -Resin roosts required little or no maintenance and were made of du rable material expected to last 20 years. Resin roosts wer also cryptic and not subject to color fading. These roosts were 8 times more expensive than wood roosts, and there was a substantial initial cost ($250) to create the roost mold. Resin roosts on the Kaibab Plateau in northern Arizona have been in place for 5 6 years, have required no maintenance or resealing roost edges, and continue to be used by bats. Wood roosts would be unlikely to persist as long as resin roosts (wood roosts may function for 10 15 years in dry climates). We noticed that wood roosts weathered (the wood discolored) within 2 years. They also would be subject to decay, especially in wetter climates. Wood roosts were more visible than resin roosts, although the could be painted to more closely simulate tree bark. However, wood roosts could be effective research tools because they are inexpensive and easy to produce. In our study, we were limited in roost placement because more snags were unsafe to climb. We were also limited in th e aspect at which the roost could be attached on a snag. Often, roosts could be placed in only a few locations on the snags. If aspect was important for roosting habitat, selecting snags and trees for roost placement should be carefully considered. It migh t be possible to design an artificial roost that wraps around the exterior of the tree (360 ) or to place multiple roosts on a tree facing several aspects so that bats could select the best aspect for roosting. Management Implications The active use of a rtificial roosts by forest bats of northern Arizona suggested a viable roosting alternative. In areas of high roost mortality from destructive agents (e.g., fire) or in areas that contain snags without desired roosting traits (e.g., exfoliating bark), arti ficial roosts might be an important management tool. For example, if natural roosts were destroyed during a prescribed fire, placing artificial roosts on surviving snags or live trees could create habitat that might help maintain a forest bat population un til natural roosts develop. Acknowledgments. This project was sponsored by Institute, with funding from the State of Arizona, the Cooperative Ecosystems Study Unit, and the Bureau of Land Management. W e thank T. Theimer, P. Z. Fulé, and W.W. Covington for their collaboration on the project and early reviews of this manuscript. We thank D. Garcia de la Cade?a, S. Knox, R. Miller, H. Shanes, G. Vance, J. Waskiewicz, and J. Wood for their assistance in obt aining, installing, and monitoring artificial roosts. The wood roost was designed by M. Rabe, the resi n roost by D. Garcia de la Cade a. We also appreciate the comments provided by 2 anonymous reviewers Literature Cited BARCLAY,R.M.R., AND R. M. BRIGHAM, e ditors. 1996. Bats and For est Symposium. Proceedings of the First International Bat Forest Interactions Symposium, 19 21 October 1995. British Columbia Ministry of Forestry, Research Branch Work Paper 23/1996,Victoria, Canada. BARCLAY,R.M.R., AND R. M. B RIGHAM. 2001. Year to year reuse of tree roosts by California bats ( Myotis californicus ) in south ern British Columbia. American Midland Naturalist 146: 80 85. BOUCHER, P. F., W. M. BLOCK,G.V.BENAVIDEZ, AND L. E. WIEBE. 1999. Implementing the expanded pre scribed fire program on the Gila National Forest, New Mexico: implications for snag management. Tall Timbers Fire Conference 20:374 379. BOYD, I. L., AND R. E. STEBBINGS. 1989. Population changes of brown long eared bats ( Plecotus auritus ) in bat boxes at Thetford forests. Journal of Applied Ecology 26: 101 112. COVINGTON,W.W., P. Z. FULÉ,M.M.MOORE,S.C.HART,T.E.KOLB, J. N. MAST,S.S.SACKETT, AND M. R. WAGNER. 1997. Restoring ecosystem health in ponderosa pine forests of the south west. Journal of Forestry 95: 23 29.

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 190 DWYER,J.K., AND W. M. BLOCK. 2000. Effects of wildfire on den sities of secondary cavity nesting birds in ponderosa pine forests of northern Arizona. Pages 151 156 in W. K. Moser and C. F. Moser, editors. Fire and forest ecology: innovative si l viculture and vegetation management. Tall Timbers Fire Ecol ogy Conference Proceedings, No. 21. Tall Timbers Research Station,Tallahassee, Florida, USA. FENTON, M. B. 1997. Science and the conservation of bats. Jour nal of Mammalogy 78: 1 14. GAINES, E . M., H. R. KALLANDER, AND J. A. WAGNER. 1958. Con trolled burning in southwestern ponderosa pine: results from the Blue Mountain Plots, Fort Apache Indian Reservation. Journal of Forestry 56: 323 327. GRINDAL,S.D., AND R. M. BRIGHAM. 1998. Short term eff ects of small scale habitat disturbance on activity by insectivorous bats. Journal of Wildlife Management 62: 996 1003. HORTON,S.P., AND R. W. MANNAN. 1988. Effects of prescribed fire on snags and cavity nesting birds in southeastern Arizona pine forests. Wildlife Society Bulletin 16: 37 44. JONES, G., P. L. DUVERGÉ, AND R. D. RANSOME. 1995. Conservation biology of an endangered species: field studies of greater horseshoe bats. Zoological Society of London Symposia 67: 309 324. LACKI,M.J., AND J. H. SCHW IERJOHANN. 2001. Day roost character istics of northern bats in mixed mesophytic forest. Journal of Wildlife Management 65: 482 488. LUGER, F. 1977. Studies on the distribution and habits of bats in nest boxes in the Geisenfeld forest, Upper Bavaria. Anze iger für Schadlingskunde Pflanzenschutz Umweltschutz 50: 183 188. (English abstract) MASER, C., R. G. ANDERSON,K.CROMACK,JR., J. T. WILLIAMS, AND R. E. MARTIN. 1979. Dead and down woody material. Pages 78 95 in J. W. Thomas, technical editor. Wildlife ha bitats in managed forests. United States Department of Agriculture Forest Service, Pacific Northwest Forest and Range Experi ment Station, Agricultural Handbook No. 553, Portland, Ore gon, USA. MEYER, W. H. 1961. Yield of even aged stands of ponderosa pin e. United States Department of Agriculture Technical Bulletin No. 630, revised. Washington, D.C., USA. PALMEIRIM,J.M., AND L. RODRIGUES. 1995. Dispersal and philopa try in colonial animals: the case of Miniopterus schreibersii . Zoological Society of Londo n Symposia 67: 219 231. PHILLIPS PLYWOOD COMPANY,INC. 2002. Hardboard. Phillips Ply wood Company, Inc. Pacoima, California, USA. Available online at: (accessed 1 Jun 2002). RABE,M.J., T. E. MORRELL,H.GREEN,J.C .DE VOS,JR., AND C. R. MILLER. 1998. Characteristics of ponderosa pine snag roosts used by reproductive bats in northern Arizona. Journal of Wildlife Management 62: 612 621. RANDALL PARKER,T., AND R. MILLER. 2002. Effects of prescribed fire in ponderosa p ine on key wildlife habitat components: preliminary results and a method for monitoring. In W. F. Lau denslayer, Jr., P. J. Shea, B.Valentine, C. P.Weatherspoon, and T. E. Lisle, technical coordinators. Proceedings of On the Ecol ogy and Management of Dea d Wood in Western Forests Con ference. 2 4 November 1999, Reno, Nevada, USA. General Technical Report PSW GTR 181. United States Department of Agriculture, Forest Service, Pacific Southwest Research Sta tion: in press. SOKAL, R. R., AND F. J. ROHLF. 1981. Biometry. Second edition. Freeman, New York, New York, USA. SWETNAM,T.W., C. D. ALLEN, AND J. L. BETANCOURT. 1999. Applied historical ecology: using the past to manage for the future. Ecological Applications 9: 1189 1206. VONHOFF,M.J., AND R. M. R. BARC LAY. 1996. Roost site selection and roosting ecology of forest dwelling bats in southern British Columbia. Canadian Journal of Zoology 74: 1797 1805. ZIEGLER, K., AND J. ZIEGLER. 1991. Success in increasing the for est bat population. Allgemeine Forst Zei tschrift 46:713 714. (English abstract).

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 191 Image 2. Big eared Bat abode Creating Bat friendly Bridges and Culverts A Resource Publication from Bat Conservation International There are several ways to provide bat friendly habitat in both new and existing brid ges or culverts at little or no extra cost to the tax payer. During construction planning, it costs nothing for an engineer to specify the appropriate crevice widths of 3/4 to 1 inches (1.9 2.5cm) in expansion joints or other crevices. Retro fitting bat fr iendly habitats into existing structures can be accomplished using the following designs. The Texas Bat Abode, Big eared Bat Abode, and the Oregon Bridge Wedge bat habitats are designed to provide day roost habitat in bridges and culverts. In the protecte d environment of a bridge or culvert, a properly constructed bat habitat made of quality materials will last for years. The Texas Bat Abode is a bridge retrofit, designed for crevice dwelling bat species. Image 1 depicts the basic structure with an exte rnal panel on either side, and 1 x 2 inch (2.5 5.1cm) wooden spacers sandwiched between 3/8 to 3/4 inch (1.3 1.9cm) exterior grade plywood partitionsns (recycled materials such as damaged plywood highway signs are ideal materials). Note that only the exter nal panels need to be cut to fit the internal spaces between the beams. The internal partitions can be square or rectangular shaped and should provide crevices at least 12 inches (31cm) deep. The wooden spacers will produce crevices with the ideal width (3 /4ths of an inch {1.9cm}). To provide foot holds, at least one side of each plywood partition is roughened (preferably both), creating irregularities every 1/8 inch (0.3cm). Many methods have been used to create foot holds, such as using rough sided panel ing, nylon screening attached with silicone caulk or rust resistant staples, mechanically scarifying the wood with a sharp object such as a utility knife or lightly grooving the wood with a saw (do not penetrate to the first plywood glue layer), lightly sa nd blasting the wood with rough grit or by coating the panel with a thick layer of exterior polyurethane or epoxy paint sprinkled with rough grit. Rust resistant wood screws should be used to assemble the spacers and partitions. Suitable locations for t he Bat Abode include open flight areas (no vegetation within 10 feet {3m}) that are not susceptible to flooding or vandalism and are at least 10 feet above the ground. Measurements of the exact location where the Bat Abode is to be placed will ensure a pro per fit. The number of partitions is arbitrary and limited only by availability of materials and the ability to support the weight of the structure. Because of the weight of the structure, it may be easiest to assemble the cut pieces in the bridge. In wood en bridges, anchor the unit to the structure by using heavy duty rust resistant lag bolts. Big eared bats of the genus Corynorhinus are frequent bridge users in both the eastern and western United States. They prefer open roost areas such as the condition s created in a large hollow tree, a darkened undisturbed room in an old abandoned house, or between the darkened beams of a quiet stream side bridge. Although untested, the Big eared Bat Abode design mimics these conditions and should attract these bats wh en properly placed. Image 1. Texas Bat Abode for crevice dwelling species

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 192 Image 3. Oregon Bridge Wedge. Designs courtesy of David Clayton and Dr. Steve Cross. For big eared bats, the Texas Bat Abode is modified with access from the bottom and spacers that are used as braces to hold the panels together. Lining the interior, nylon screening attached with staples provides foot holds for roosti ng bats. ( Image 2 ) Unlike crevice dwelling bats, big eared bats prefer low bridges with thick vegetation growing alongside. The Big eared Bat Abode should be placed at least 6 to 10 feet (2 to 3 m) above the ground in a secluded, vegetated portion of the b ridge with care taken not to block access to the fly way entrance. The big eared Bat Abode can be partially assembled on the ground leaving one end panel off until it is placed in its chosen location. If for a wooden bridge, the unit can be anchored to t he bridge using heavy duty lag bolts. Because big eared bats are very sensitive to disturbance, it is recommended that units be placed in areas of low activity and painted in such a manner as to avoid attracting attention. The Oregon Bridge Wedge ( Image 3 ) is an inexpensive method of retro fitting bridges or culverts with day roost habitat for bats. A single piece of 3/8 or 3/4 inch (1 2 cm) untreated exterior plywood or suitable recycled material (e.g.; damaged highway signs) is cut to the dimensions of a t least 18 inches high by 24 inches wide (46 x 61 cm). Backed with three 1 x 2 inch (2.5 x 5 cm) wood strips along the top and sides these panels can then be epoxied to a protected part of a bridge or culvert. Using galvanized wood screws, attach the plyw ood panel to the wood strips which are cut to fit the top and sides of the panel, leaving an opening along the bottom. Larger or smaller sized panels can be used. Studies have shown that bats prefer crevices 12 inches (31 cm) or greater in depth. If larger panel sizes are used, place the vertical wooden strips every 24 inches (61cm) to support the plywood and prevent warping. Installation of light weight (~10 lb {4.5 kg}) Wedges can be done by applying a thick layer of fast drying environmentally safe epo xy cement (such as 3M Scotch coat 3 12) to the 1 x 2 inch strips. When the epoxy becomes tacky (~20 30 minutes @ 60°F {16°C}) hold the panel in position until it cures enough to support the weight. Hint: Check the installation site first to make sure the s upport strips fit flat or nearly so against the concrete surface. Also, to avoid having to hold the entire panel in position while the epoxy cures, the largest support strip can be adhered to the preferred site prior to assembling (a thick layer of clear s ilicone caulk can be used here). While that piece is curing, assemble the remaining panel, coat it with epoxy and attach it to the pre adhered strip. If the panel is to be attached to wood, then use appropriate rust resistant wood screws. Larger sized pan els can be used, but additional weight, may necessitate an increase in the support strip width (from 1 x 2 inch strips to 1 x 4 {2.5 x 10 cm} or 1 x 6 inches {2.5 x 15 cm}), thereby increasing the panel to bridge epoxy surface area. We also encourage exper imentation with the 3/4 inch (2.5 cm) spacing. Although 3/4 inch spaces seem to provide the most versatile bat friendly widths for North American species, larger species, such as the big brown bat, will use wider crevices. To retain the secluded feeling in the panel, the entrance should remain restricted to 3/4 inches with only the top beveled out wards. Wedge placement is possible on any adequately sized, flat concrete or wood surface. However, it is recommended that the panels be placed nearest to the su n warmed road slab (preferably as high as possible between heat trapping bridge beams), at least 10 feet high (3 cm), with a clear flyway (at least 10 feet) , and out of view or reach of potential predators or vandals. Ideal bridge locations include, but a re not limited to, columns, bent caps, diaphragms, and the sides of beams. The Wedge can also be installed in the middle sections of appropriately sized culverts (> 5 feet (1.5 cm) in height). It

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 193 Image 4. Bat domed culvert. Graphics courtesy of Texas Department of Transportation. is not recommended to place a Wedge in any structure that ha s the potential for flooding. As a precaution, a 1.5 inch (3.8 cm) gap can be left between where the side and top support strips join to act as an escape route in the event of fast rising water. The Bat domed culvert ( Image 4 ) is a modified concrete box culvert designed to provide a secluded bat friendly "domed" ceiling. The dome has several bat friendly characteristics; the height is increased, warm air is trapped, and the light intensity and air movement is reduced. Studies of bat use of concrete culv erts indicate that bats prefer long concrete culverts with roughened walls and ceilings greater than 3 feet (0.9 meters) in height. Bat domed culverts should be constructed from concrete box culverts at least 4 feet (1.2 meters) in height with an additiona l 2 foot (0.6 meter) raised portion centered in the culvert with the raised area representing 1/4 of the entire length of the culvert. Bat roosts on culvert walls and ceilings are often associated with irregularities. The walls and ceilings of the domed ar ea should be roughened to enhance the value to bats. A method of attaching panels or partitions, such as female threaded inserts, can be incorporated into the dome walls and ceiling for creating opportunities for additional surface areas once the culvert i s completed. The bat domed culverts should not be placed in areas susceptible to flooding. Consult with the engineers to evaluate the potential for flooding. However, in the event of rising water, it is believed that the dome can serve as a temporary ai r trap, preventing water from reaching the roost area for short periods. This document is also available on the BCI webpage: http//

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 194 Artificial Roosts and Other Conservation Initiatives for Bats: On line Resources from BCI Topics Incl ude: Bat Houses FAQs Installation BCI Certification Program Community Roosts Custom Roosts The Bat House Researcher Many Free Downloads! Critera for Successful Bat Houses Tips for Attracting Bats Bat House Bats FAQs About Bats Bats and Public Health Getting Rid of Wasps Bats and Mosquitoes Single Chamber Bat House Plans Installation Methods Bat House Researcher Archives . . . and much more! Bats & Mines Conservation Activi ties Partial list of bats and mines conservation projects initiated by BCI over the years. Resources Bats and Mines, Resource Publication and Bats and Mines brochure free downloads! Upcoming Events listing of current bats and mines conferences, wor kshops, and working group activities Bats & Wind Energy resources, events, and featured technical and scientific publications about bats and wind energy conc erns. Bats in Bridges Bats in American Bridges, Resource Publication free download! Cave Conservation Protection and Resoration information about underground environments for bats. Resources: Field Guide to Eastern Cave Bats and Cave Conservation and R estoration Water for Wildlife Water for Wildlife, Resource Publication free download! And a complete listing of the Goals and Objectives, Research and Conservation, Collaboration and Training, and Bibliography and Links for more information about bats a nd western water concerns.

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BCI Bat Conservation and Management Workshop Arizona © 2011 Bat Conservation International Page 195 Glossary of Scientific Names Given to Bats After: Barbour, R.W. and W.H. Davis, 1969. Bats of America . University Press of Kentucky, 286 pp. Antrozous (an tro zoh us) cave animal Artibeus (ar tib ee us) hanging from the tibia auriculus (a rick u lus) the external ear austroriparius ( aus troh rye pare ee us) frequenting southern stream beds blossevillii (bloss a vill ee eye) rusty furred borealis (bor ee al is) of the north; northern brasili ensis (bra zill ee en sis) belonging to Brazil californicus (cal a forn a cus) proper name: California Choeronycteris ( care o nick ter is) nocturnal pig ciliolabrum ( sill ee oh lay brum) hairy lips cinereus (sa near ee us) -ash colored Corynorhi nus (core ee no rine us) club nosed curasoae (cur a soh ee) proper name: Curacao ega ( ee ga) proper name: Ega Eptesicus (ep tess a cus) flying Euderma (you derm a) -good skin Eumops ( you mops) good bat evotis (ee voh tis) good ear femorosaccu s ( fem oh row sock us) -sack on the thigh fuscus ( fuss cuss) brown glaucinus (glau sine us) silver, gray, gleaming grisescens (gri sess sens) beginning to gray hesperus ( hes per us) the land west; western humeralis (hume er al is) pertaining t o the humerus Idionycteris (id ee oh nick ter is) distinct or peculiar and nocturnal intermedius (in ter meed ee us) intermediate; occupying the middle jamaicensis (ja may ken sis) proper name: Jamaica keenii (keen ee eye ) -proper name: Keen Lasio nycteris (lay zee oh nick ter is) hairy and nocturnal Lasiurus (lay zee your us) -hairy tail leibii ( lee bee eye) proper name: Leib Leptonycteris (lep toh nick ter is) slender and nocturnal lucifugus (loo ciff a guss) fleeing light macrotis (ma crow tis) large ear Macrotus (ma crow tus) large ear maculatum (mac you lay tum) spotted megalophylla (meg a low file lah) large leaves melanorhinus (mel an oh rye nus) black nose mexicana (mex a can a) proper name: Mexico molossus (mow loss su s) mastiff Mormoops (more moops ) monster bat Myotis (my oh tis) mouse ear nivalis (ni val is) -snowy noctivagans (nock ti vah gans ) night wandering Nycticeius (nick tee zee us) night hunter Nyctinomops (nick tin oh mops) -night bat occultus (oh cult tus) hidden, obscure pallidus ( pal id us) -pale perotis (per oh tis) maimed ear phyllotis (fye low tis) leaf ear Pipistrellus (pip a strell lus) a bat Plecotus (pla coh tus) twisted ear rafinesquii (raff a nesk kee eye) proper name: Rafinesque sanborni ( san born eye) proper name: Sanborn seminolus ( sem a nole us) proper name: Seminole septentrionalis (sep ten tree oh nal is) belonging to the north; northern sodalis (so dal is) a comrade subflavus (sub flave us) somewhat yel low Tadarida (ta dare a dah) withered toad thysanodes ( thigh sa noe dees) with a thing like a fringe townsendii (town send ee eye) proper name: Townsend underwoodi ( un der wood eye) -proper name: Underwood velifer ( vel if fer) bearing a veil vol ans ( voh lans) flying waterhousii (wa ter house ee eye) proper name: Waterhouse xanthinus (zan thigh nuss) yellowish yumanensis ( you ma nen sis) belonging to Yuma (Arizona)

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© 2011 Bat Conservation International Page 196 ACOUSTIC INVENTORY DATA SHEET Location: Lat (N ): Long (W): UTM (E): UTM (N): Date: Time: Recorder: Temp: Wind: Sky: Sunset: Moon: Moonrise Moonset: Stationary Monitoring Habitat Description: Time: Passes: Stationary Monitoring Habitat Description: Ti me: Passes: Stationary Monitoring Habitat Description: Time: Passes: Walking/Driving Transect Habitat: Time: Distance: 0.00 Passes: Walking/Driving Transect Habitat: Time: Distance: 0.00 Passes: Walking/Driving Transect Habitat: Time: Distance: 0.00 Passes: Notes: SPECIES REPRESENTATIVE FILENAME COMMENTS

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© 2011 Bat Conservation International Page 197 BAT CAPTURE DATA FORM Location (state, county, town): Date: Start Time: End Time: Recorder: Lat/Long: Start Temp: End Temp: %clouds: Habitat: ___________________________________________ ______ ___________ Capture Technique : (# and type) __ _ _ 2.6m net _ ___6m net ____9m net ____12m net ____ Harp Tra p _________ Other Set Over/Near Water: YES/NO ( put diagram on back ) Please use separate data forms for net caught vs. trap caught bats; or otherwise indicate bats caught w ith different methods. TIME SPECIES SEX (M/F) AGE (J/A) REPRODUCTIVE STATUS ( M: S/NR) ( F: P/L/PL/NR) FA (MM) EAR (MM) WEIGHT (G) CAP (H/N) BAND OR MARKING (COMMENTS) 1. 2. 3. 4. 5. 6. 7. 8. 9. 10. 11. 12. 13. 14. 15. PLEASE DRAW DIAGRAM OF SET UP ON BACK. NOTES ON BACK: YES NO PAGE ____ OF ____ STAFF: __________________

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© 2011 Bat Conservation International Page 198 I NSTRUCTIONS FOR FILLING OUT BAT CAPTURE DATA FORMS rranged in tandem (e.g., end to end) or in various geometric configurations (e. g., parallel, V formation, stacked (double , triple , or quad high), etc). Bats that eparate data forms or by identifying them with caught bats). If a single data form is used to record bats from more than one site, then the entire set up MUST be diagramed on the back of the sheet with each site clearly identified (e.g., A, B, C, or 1, 2, 3) AND then captures from each site clearly identified on the front of the sheet. Specific information about each line item on the bat capture data form can be found below. Metadata STAFF: Each night at least on ns about the data crop up during analysis or reporting. LOCATION: Include the two letter state abbreviation first on this line the n consult the STAFF to confirm the county, nearest town, and area. BCI Staff will maintain complete DATE: Include day, month, and year information. Print out name of month (i.e., do not use an ordinal). START TIME/EN D TIME hour clock), and record the time at which the set up is complete (not the time at which the first bat is caught) as the RECORDER: Include full name of person (people) responsible for filling out data on form. GPS: Use provided equipment to get an exact GPS location at the net/trap (or from the middle of a complex net/trap setup). GPS Datum: o acquire the GPS location (e.g., NAD27 (preferred), NAD83, WGS84 or specify another convention). START TEMP/END TEMP: Record temperature both at time of set up and take down. Report temperatures in °C. % CLOUDS: Estimate amount of cloud cover as follow s: clear = 0%, partly cloudy <50%, mostly cloudy >50%, overcast/cloudy = 100%. HABITAT : Describe the habitat within 150 m of the site. Include topography (riverbed, meadow, hilltop, etc.) and vegetation, indicat ing dominant tree/plant species. WEATHER/W IND: Include weather data such as fog, mist, intermittent rain, steady rain, thunderstorms, snow etc., and qualify wind conditions as follows: calm (no discernable wind), breezy (leaves rustling), windy (trees swaying). CAPTURE TECHNIQUE (# and type): Spe cify net or trap, include numbers of nets/traps and lengths/sizes if multiple nets/traps are used, Indicate if nets are doubl e , triple , or quad high by recording them as 2H, 3H, or 4H respectively. If unique configurations or geometric combinations are u sed, be sure to diagram the setup(s) on the back of the sheet, identify each set up of more than one net, trap, or net and trap by number or letter and index each individual caught in that set up by the same number on the front of the sheet in the SET colu mn. SET OVER/NEAR WATER (pool and swoop zone dimensions): Estimate pool size (width and length) in meters either by pacing off the dimensions or by comparing the pool size to the net length(s) used. Record the swoop zone by calculating the total size of t he unimpeded approach to and from the pool.

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© 2011 Bat Conservation International Page 199 DIAGRAM OF SET UP ON BACK: If more than one net is used at a site, the set up must be diagramed on the back. Multiple set ups MUST be identified by a unique letter or number for each set up, with corresponding c aptures identified for each set up using the same identifiers on the front of the sheet. Data Columns TIME: Capture time for each individual should be recorded as soon as removal begins, using a 24 hour (military) clock. Capture times for trapped bats sho uld be the same for every individual removed during a single checking effort, unless exact capture time is observed. SET: If multiple nets are set at a single site, then each set up (of a single net/trap or group of nets/traps) need to be identified and i ndexed by letter or number in a diagram on the reverse of the form. Captured bats must then be identified by set up using the same letter or number index. SPECIES: Species names are recorded using a 6 letter code where the first three letters represent ge nus and last three letters represent species (e.g., Myotis lucifugus = MYOLUC). SEX: AGE: Age phalangeal joints (knuckle bones) in the fingers. Joints appearing bulbous, opaque, and dense indicate adults, and joints appearing elongated, trans lucent, and undeveloped. This is most easily observed when back lit by a weak light (e.g., a mini Mag light). REPRODUCTIVE STATUS: s nr = no visible evidence of reproduction). Females are p = when palpated, abdomen appears distended and skull or forearm of fetus can be discerned, a swollen abdomen without obvious fetal parts indicates a bat with hibernation or migratory fat and is considered non reprod l = nipples, located in under arm region, are obvious, swollen, and milk can pl = nipples are obvious, hair around them has been rubbed off, yet they are limp and no milk can be expressed nr = no visible evidence of reproduction). MEASUREMENTS (FA, EAR, TR*, HF*, WT): Measurements are taken with millimeter rulers, calipers, spring scales, or digital scales provided. Forearms ( FA ) are measured from the wrist to the elbow joint and are easiest to do on a folded wing. Ears ( EAR ) are measured from the notch at the base to the tip. Long eared bats often curl their ears back and these will have to be un rolled along the length of the ruler for an accurate measurement (ca lipers are difficult to use for ear measurements). Tragus lengths ( TR ) are measured from the base to the tip. Hind foot lengths ( HF ) are measured from the ankle joint to the tips of the toes. Weights ( WT ) are easiest to obtain when bats are confined in a bag or tube (which will be provided) it is important to subtract the tare weight of the container before reporting the actual weight of the bat. All lengths are reported in millimeters (mm) and weights are reported in grams (g). * importan t only for T&E or TNW species. BAND/TAG/NOTES: If you are asked to permanently band or tag a bat, complete details of the band/tag must be recorded. For bands, this include s the band material (usually metal or plastic), the color, the inscription, and whe re the band was applied (generally males are banded on the right, females on the left). If a bat has been is radio tagged, then the frequency (in mHz) is recorded. This space can also be used for any other distinguishing characteristics (e.g., molt patt erns, injuries, temporary markings, or unusual observations). Other DIAGNOSTIC PHOTO AVAILABLE: In cases of extensions) photographic documentation might be warranted. In these cases, macro or other suitable close up pictures should be taken of diagnos tic characteristics (e.g., calcars, tragi, dentition, fur patterns, bands, etc.) along with a full face portrait. Images must be indexed to the capture record and filed with permit reports. NOTES ON BACK: If a diagram of the net set up is included OR if data or any other information is recorded on the reverse of the form then it is important to indicate as such on the front. This ensures that if forms are copied in the future, information on the reverse is also included. PAGINATION: If additional pages ar e needed to record all the data from a site, then they should be numbered sequentially and the total number of pages indicate d in the blanks in the bottom right corner. Be sure that at least the Recorder name and the Location information is copied at the t op of each additional page so the data does not become confused between sites on a given night.

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© 2011 Bat Conservation International Page 200 BAT CAPTURE DATA FORM Additional Data for Myotis californicus and Myotis ciliolabrum Location (state, county, town, area): Date: Reference to Original Cap ture Form: Recorder(s): Source: Hoffmeister, Mammals of Arizona and Schmidly, Bats of Texas J.Mamm 80(1): 11 23 Bat # Fur Thumb Length Thumb Appearance Mask Forehead Tail Muzzle Ech o Call Conclusion Characters to Observe Myotis californicus Myotis ciliolabrum Fur Appearance Short and dull w/reddish tips appearing bi colored Long and glossy w/shiny tips appearing tri colored Length and Shape of Thumb < 4.2mm, thin and scrawny > 4.2mm, thick and robust Mask Made by Face and Ears Ears and muzzle becoming lighter, especially near eyes making a less distinct mask Ears and muzzle uniformly dark even around eyes, making a distinct mask Slope of Forehead Abrupt Gently slopi ng Tail Membrane and Tail Tail does not protrude past tail membrane Tiny tip of tail protrudes past tail membrane Appearance of Muzzle when Viewed from Above Muzzle short; about same length as the width of the nostrils Muzzle long; about 1.5 x as long a s the width of the nostrils Echolocation Call: Min. Freq. 50 kHz 40 kHz M. californicus M. ciliolabrum

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© 2011 Bat Conservation International Page 201 Recommended Survey Methods Matrix for Western Bat Species Developed by the Western Bat Working Group Durango/2002 Scientific name Common name Capture Survey Passive Ac tive Comments Mormoops megalophylla faced bat 2 2 1 1 Capture: Readily captured in nets, but very delicate and often die. Suggest using harp traps. ID: Morphologically distinct. R oost Location: Roosts in caves ID: Presumably easy to locate a nd ID when present. Passive Acoustic Detection: Easy to detect acoustically. ID: Calls highly diagnostic. Active Acoustic So distinctive acoustically that visual observation does not contribute to ID. Choeronycteris mexicana Mexican long tongued bat 3 3 U 4 Capture: Effectiveness of netting depends on habitat type. ID: Morphologically distinct. Roosts Location: Difficult to find. ID: Easy to detect in roost. Passive Acoustic Detection: Difficult to detect acoustically. ID: Issues currently unresolved. A ctive Acoustic Indistinguishable from Leptonycteris species, except at very close range (e.g., hummingbird feeders). Leptonycteris yerbabuenae lesser long nosed bat 3 1 U 4 Capture: Effectiveness of netting depends on habitat type .ID: Morphologically di stinct. Roost Location: Roosts in mines and caves; highly colonial. ID: Easy to detect and ID in roost except in areas of overlap with L. nivalis . Passive acoustic Detection: Difficult to detect acoustically. ID: Issues currently unresolved. Active acousti c Indistinguishable in flight from L. nivalis and Choeronycteris, except possibly at very close range (e.g., hummingbird feeders). Leptonycteris nivalis greater long nosed bat 3 1 U 4 Capture: Effectiveness of netting depends on habitat type. ID: Morphol ogically distinct. Roost Location: Roosts in mines and caves; colonial. ID: Easy to locate and ID, except in areas of overlap with L. curasoae. Passive Acoustic Detection: Unknown, but presumably difficult to detect acoustically. ID: Issues currently unres olved. Active Acoustic Indistinguishable in flight from L. curasoae and Choeronycteris , except possibly at very close range (e.g., hummingbird feeders). Macrotus californicus California leaf nosed bat 4 1 4 4 Capture: Avoids mist nets. ID: Morphologically distinct. Roost Location: Most effectively found by searching for colonial roosts, primarily in mines and caves. ID: Easy to locate and ID in roost. Passive Acoustic Detection: Difficult to detect acoustically. ID: Subset of calls diagnostic. Active Aco ustic Can ID visually at close range. Antrozous pallidus pallid bat 1 3 2 1 Capture: Fly low to ground and readily captured in nets (often in upland habitats). ID: Morphologically distinct. Roost Location: Easy to detect colonies in man made roosts; diff icult in most natural roosts (e.g., trees and rock crevices). Frequently uses man made roosts (mines, bridges, buildings) in parts of its range. Often found in night roosts, especially mines and bridges. ID: Roost consp icuously, easy to ID. Guano with char acteristic culled insect parts (particularly Jerusalem crickets and scorpions) often distinctive. Passive Acoustic Visually distinctive.

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© 2011 Bat Conservation International Page 202 Scientific name Common name Capture Survey Passive Ac tive Comments Corynorhinus townsendii eared bat 3 2 4 4 Capture: Effective at avoiding mist nets. ID: Morphologically similar to I. phyllotis . Roost Location: Most effectively found by searching for colonial roosts, in mines and caves. Roosts in buildin gs in coastal portion of range. Some portions of range, i.e., Canada and some desert areas, roosts very difficult to locate. ID: Easy to locate and ID in roost. Passive Acoustic Detection: Difficult to detect acoustically, ). ID: Calls, when detected, are diagnostic. Active Acoustic Visually distinctive in most settings. Euderma maculatum spotted bat 3 5 2 1 Capture: Can be effective where water is a limiting factor in xeric conditions, although netting is not effective in many portions of range. ID: Morphologically distinct. Roost Location: Non colonial, cliff roosting; very difficult to locate and generally inaccessible. ID: Unknown; no roosts have been visually inspected; only locations have been from a distance using rad io telemetry. Passive acoustic Detection: Easy to detect acoustically (w/microphones sensitive to audible frequencies). Calls are audible. ID: Most sequence s diagnostic, except in area of geographic overlap w/ I. phyllotis . Active acoustic Difficult to dis tinguish from I. phyllotis ; otherwise distinctive in flight. Eptesicus fuscus big brown bat 1 3 3 1 Capture: Readily captured in mist nets, but problematic in open areas, especially where water is abundant. ID: Morphologicall y distinct. Roost Location: Ea sy to locate man made roosts; difficult in most natural roosts (e.g., trees and rock crevices). Natural roosts dominate throughout much of range. Night roost surveys effective. ID: Colonies often conspicuous, species easy to ID. Passive Acoustic Detection : Easy. ID: subset of sequences diagnostic acoustic overlap with Lasionycteris and Tadarida . Active Acoustic Visually distinctive in flight. Idionycteris phyllotis eared bat 3 3 2 2 Capture: Captured infrequently in mist nets; show loyalty t o particular water sources, but may be difficult to locate in initial surveys. ID: Morphologically similar to C. townsendii . Roost Location: Easy to detect in man made roosts (e.g., mines); difficult in natural roosts (e.g., trees, rock crevices). ID: Eas y: roost in clusters on open surface (e.g., domes of mines). May be confused with C. townsendii . Passive Acoustic Detection: Easy to detect acoustically (with low frequency microphone). ID: Most sequences diagnostic, except can be difficult to distinguish from E. maculatum . Geographic overlap with E. maculatum throughout much of its range. Highly distinctive social call. Active Acoustic Can be difficult to distinguish from E. maculatum . Lasionycteris noctivagans silver haired bat 1 5 4 2 Capture: Vulnera bility to net capture varies with habitat, but generally quite susceptible to capture. Captured over water sources (large and small). ID: Morphologically distinct. Roost Location: Very difficult to locate in natural roosts (e.g. trees and snags). ID: Unli kely to locate via roost search but, can be distinguished visually in flight upon exit. Passive Acoustic Detection: Easy to detect acoustically. ID: Some calls distinctive, but overlap with Tadarida and Eptesicus . In areas without Tadarida , many sequences are diagnostic. Active Acoustic With experience can be distinguished visually in flight. Lasiurus blossevillii western red bat 3 5 2 1 Capture: Sometimes captured in mist nets, but foraging areas often not suitable for netting (e.g., over large water so urces). ID: Morphologically distinct except where overlaps with L. borealis . Roost Location: Non colonial. Very difficult to locate tree roosts. ID: Difficult to locate bats in foliage, easy to ID except where overlaps with L. borealis . Passive acoustic Detection: Easy to detect acoustically. ID: Most sequences diagnostic in areas w/o L. borealis . In areas with L. borealis , extensive acoustic overlap, but probably distinguishable statistically. Some acoustic overlap with P. hesperus . Active Acoustic Dist inctive in flight except in areas w/ L. borealis .

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© 2011 Bat Conservation International Page 203 Scientific name Common name Capture Survey Passive Ac tive Comments Lasiurus borealis eastern red bat 2 5 2 1 Capture: Readily captured over water and in side channels in eastern U.S. ID: Morphologically distinct except where overlaps w /L. blossevillii . Roost Location: Dif ficult to locate tree roosts. ID: Difficult to locate bats in foliage, easy to ID except where overlaps w/ L. blossevillii . Passive Acoustic Detection: Easy to detect acoustically. ID: Sequences diagnostic in areas w/o L. blossevillii . In areas w/ L. blosse villii , extensive overlap, probably distinguishable statistically. Active Acoustic Distinctive in flight except in areas w/ L. blossevillii . Lasiurus cinereus hoary bat 3 5 2 1 Capture: Fly high; often under represented in net captures. Often foraging in a reas that cannot be feasibly netted. ID: Morphologically distinct. Roost Location: Non colonial. Very difficult to locate tree roosts. ID: Difficult to locate bats in foliage but easy to distinguish from other species. Passive Acoustic Detection: Easy to detect acoustically. ID: Many calls diagnostic throughout much of its range; subset of calls overlap with Tadarida and N. femorosaccus . Active Acoustic Distinctive in flight. Lasiurus xanthinus southern yellow bat 3 3 2 1 Capture: Readily captured in s ome habitats; apparently difficult in others. Not enough known about appropriate habitats. ID: Morphologically distinct. Roost Location: Difficult to locate tree roosts. Can sometimes be located by monitoring palm trees at dusk. ID: Difficult to observe i n roost, but easy to ID during emergence from roost. Passive acoustic Detection: Easy to detect acoustically. ID: Most sequences diagnostic, but some acoustic overlap w/ L. borealis and E. fuscus . Active acoustic Reasonably distinctive in flight. Myotis auriculus southwestern myotis 1 5 U U Capture: Readily captured in mist nets. ID: Morphologically distinct except where range overlaps with M. evotis . Roost Location: Easy to detect in man made roosts; difficult in most natural roosts. Likely that natural roosts dominate. ID: Roost in small groups. Requires handling for positive identification. Passive Acoustic Detection: Easy to detect acoustically. ID: Probably many sequences diagnostic except in area of geographic overlap with Myotis evotis. Active Aco ustic Visual cues will not help distinguish from M. evotis . Myotis californicus California myotis 1 4 3 1 Capture: Readily captured in mist nets. ID: Morphologically similar to M. ciliolabrum . Can be distinguished from M. ciliolabrum by combination of ca pture and recording of hand release echolocation call. Roost Location: Can be found in man made roosts, but generally non colonial and crevice roosting; most roosts not man made and difficult to find. Sometimes found in night roosts. ID: Requires handling for positive identification. Passive Acoustic Detection: Easy. ID: Difficult to distinguish from M. yumanensis (50 kHz Myotis ). Active Acoustic: Flight behavior distinguishes it from M. yumanensis in most settings. Myotis evotis long eared myotis 1 3 2 2 Capture: Readily captured in mist nets at both aquatic and terrestrial sites. ID: Morphologically distinct except in areas of overlap w/ M. auriculus , M. keenii , or M. septentrionalis . Also similarity to M. thysanodes in some regions. Roost Location: Can be detected in man made roosts, but often cryptic, difficult in most natural roosts (e.g., trees, rock crevices). Natural roosts dominate. Somet imes in night roosts, particularly mines and bridges, although extent to which these features are used varies r egionally. ID: Small colonies. Generally crevice roosting. Often requires handling for positive identification. Passive Acoustic Detection: Intermediate intensity calls. ID: Subset of sequences diagnostic except in area of geographic overlap w/ M. auriculu s , M. septentrionalis or possibly M. keenii . Also possible confusion under some habitat conditions w/40 kHz Myotis . Active Acoustic May be helpful in distinguishing it from short eared Myotis.

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© 2011 Bat Conservation International Page 204 Scientific name Common name Capture Survey Passive Ac tive Comments Myotis ciliolabrum small footed myotis 2 3 4 4 Capture: Readil y captured in nets in some portions of its range; but vulnerability to netting may vary regionally. ID: Morphologically similar to M. californicus . Can be reliably identified using combination of morphological and acoustic data. Roost Location: Mostly non colonial. Frequently in mines, but natural roosts likely dominate, and difficult to find. Sometimes found in night roosts. ID : Roost in small groups. Requires handling for positive ID. Passive acoustic Detection: Easy to detect acoustically. ID: Not curren tly distinguishable from other 40 kHz Myotis . Active acoustic Can sometimes be distinguished when observed in flight, but requires experience. Myotis keenii 4 5 U U Capture: Difficult to find. Most netting records from known cave roosts. ID: Issues currently unresolved, but probably difficult to distinguish from M. evotis . Due to uncertainties regarding ID, morphometric data, hand release calls, and wing biopsy should be collected from all individuals. Roost Location: Can be detected in caves and buildings, but difficult in tree roosts. Tree roosts probably dominate. ID: Small colonies and difficult to distinguish from M. evotis . Often requires handling for positive ID. Passive Acoustic Detection: Presumably has intensity similar to M. evotis . ID: Issues currently unresolved, but likely difficult to distinguish from M. evotis Active Acoustic Unknown Myotis lucifugus little brown myotis 2 3 4 3 Capture: Readily netted in some areas; net avoidant in others. ID: Morphologically similar to M. yu manensis and M. occultus . Can be reliably identified using combination of morphological and acoustic data. Roost Location: Frequently in man made roosts (mines, bridges, buildings) in parts of its range. Difficult to find in most natural roosts (e.g., tre es and rock crevices). Sometimes found in night roosts. ID: Highly colonial and easy to detect in man made roosts. Often requires handling for positive identification. Passive Acoustic Detection: Easy to detect acoustically. ID: Some calls/sequences diagn ostic, though probably not distinguishable from M. occultus in areas of geographic overlap. Difficult to distinguish from other 40 kHz Myotis. Active Acoustic Flight behavior sometimes distinctive, particularly over water. Myotis lucifugus occultus Arizo na myotis 2 3 4 4 Capture: Fairly easy to capture in nets. ID: May be difficult to distinguish from M. lucifugus in areas of overlap. Roost Location: Roost in man made roosts, but natural roosts dominate. Can often be found in night roosts. ID: Easy to de tect in man made roosts; difficult in most natural roosts. Often requires handling for positive ID. Passive acoustic Detection: Easy to detect acoustically. ID: Issues currently unresolved but probably difficult to distinguish acoustically from other 40 k Hz Myotis . Active Acoustic Difficult to distinguish visually. Myotis septentrionalis Northern myotis 3 3 2 2 Capture: More successful in interior forest than over water in eastern deciduous forest; harp traps set in gaps between trees effective in SD and WY. Occasionally captured over water. ID: Easy except where range overlaps with M. evotis. Roost Location: Surveys for night roosts and hibernacula can be effective; day roosts under bark. ID: Very cryptic in day roosts. Requires handling for positiv e ide ntification. Passive Acoustic Detection: Intermediate intensity calls ID: Many sequences diagnostic, but overlap with other 40 K Myotis, particularly M. lucifugus. Also potential for confusion with M. evotis. Active Acoustic May be helpful in distinguish ing it from small eared Myotis. Often flies in cluttered settings where ID can be difficult.

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© 2011 Bat Conservation International Page 205 Scientific name Common name Capture Survey Passive Ac tive Comments Myotis thysanodes fringed myotis 1 3 2 2 Capture: Readily captured in mist nets (often on secondary streams in northwestern portion of range). ID: Generally easy , but morphologically similar to M. evotis in some regions. Roosts Location: Can be detected in man made roosts, but difficult in most natural roosts (e.g., trees, rock crevices). Natural roosts dominate. Sometimes found in night roosts. ID: Small colonie s and often in crevices. Requires handling for positive ID. Passive Acoustic Detection: Intermediate intensity calls. ID: Many sequences/calls diagnostic. Possible confusion with A. pallidus . Active Acoustic Flight behavior, in combination with call morp hology, sometimes helpful. Myotis velifer cave myotis 2 1 3 3 Capture: Limited usefulness in some habitats. ID: Morphologically distinct, but potentially confused with M. occultus or M. l ucifugus. Roost Location: Primarily in caves and rock crevices, bu t occasionally in buildings. ID: Roost colonially; can be confused with other colonially roosting Myotis and E. fuscus . Passive Acoustic Detection: Easy to detect acoustically. ID: Overlap with other 40K Myotis. Acoustic ID best in areas without other 40 kHz Myotis . Active Acoustic Visually similar to other 40 kHz Myotis . Myotis volans long legged myotis 2 2 4 3 Capture: Effectiveness of netting varies regionally, and setting makes a difference. ID: Morphologically distinct. Roost Location: Can be found in man made roosts; difficult in most natural roosts. Natural roosts dominate. Often found in night roosts. ID: Requires handling fo r positive identification. Passive Acoustic Detection: Easy to detect acoustically. ID: Issues currently unresolved with o ther 40K Myotis. Active Acoustic Flight behavior can be distinctive (long tail membrane). Myotis yumanensis Yuma myotis 1 2 3 1 Capture: Water skimming foraging style makes this species highly vulnerable to capture in mist nets set over still water. ID: Morphologically similar to M. lucifugus and M. occultus . Can be distinguished from M. lucifugus and M. occultus by combination of capture and recording of hand release echolocation call. Roost Location: Commonly in man made roosts. Form large aggregations in night roosts (particularly bridges). Difficult to locate most natural roosts. ID: Highly colonial and easy to detect in man made roosts. Requires handling for positive identification. Passive Acoustic Detection: Easy to detect acoustically. ID: Diffic ult to distinguish from M. californicus, though some calls diagnostic (50K Myotis). Active acoustic Flight behavior, particularly water skimming, distinctive. Parastrellus hesperus (formerly Pipistrellus hersperus ) canyon bat (formerly western pipistrell e) 2 5 1 1 Capture: Captured in nets fairly readily, although often fly high. ID: Morphologically distinct. Roost Location: Predominantly cliff roosting. Some roosting in man made structures, particularly mines. ID: Usually non colonial or small colonies. Can be identified visually at very close range. Passive acoustic Detection: Easy to detect acoustically. ID: Most calls diagnostic, although some overlap with L. blossevillii. Active Acoustic Visually distinctive. Eumops perotis greater mastiff bat 3 3 1 1 Capture: Effectiveness of netting varies regionally. Have been netted where open flight paths are evident, or water is limiti ng. Forage at considerable height; captured at drinking sites. ID: Morphologically distinct. Roost Location: Most roost in cli ffs, thus highly inaccesible; quite frequently in building roosts. Can be found by surveying for guano and listening for loud chatter along base of cliffs. ID: Generally requires monitoring at emergence. Passive Acoustic Detection: Easy to detect acoustic ally (better w/low frequency microphone). Calls in the audible range for many people. ID: Calls diagnostic. Active Acoustic Distinctive except in areas of overlap w/ E. underwoodi .

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© 2011 Bat Conservation International Page 206 Scientific name Common name Capture Survey Passive Ac tive Comments Eumops underwoodi 3 U 1 1 Capture: Logistically d ifficult, requiring net sets over large bodies of water. ID: Morphologically distinct. Roost Poorly known; one study radio tracked to saguaro cactus. Passive Acoustic Detection: Easy to detect acoustically (better with low frequency microphone). Calls in t he audible range for many people. ID: Calls diagnostic except where range overlaps with N. macrotis . Active Acoustic Distinctive except in areas of overlap with E. perotis and N. macrotis . Nyctinomops femorosaccus pocketed free tailed bat 3 3 2 1 Capture : Effective in low elevation canyon sites, and near known roosts. ID: Morphologically distinct, but potentially confused with T. brasiliensis. Roost Location: Roosts often inaccessible. Roosts primarily in cliffs. Sometimes possible to find roosts by surv eying for guano and listening for chatter at base of cliffs. ID: Generally requires monitoring at emergence. Passive Acoustic Detection: Easy to detect acoustically; calls in the audible range for some people. ID: Subset of calls/sequences diagnosti c, some overlap with both Tadarida and L. cinereus . Active Acoustic Useful for distinguishing from L. cinereus . Nyctinomops macrotis big free tailed bat 3 5 1 1 Capture: Records extremely limited suggesting serious challenges. ID: Morphologically distinct . Roost Location: Generally cliffs and rock crevices; often inaccessible. Also known to use building and tree roosts. Guano deposits and chatter can potentially be used to locate roosts, but generally not effective. ID: Generally requires monitoring at em ergence. Passive Acoustic Detection: Easy to detect acoustically (best with low frequency microphone); calls in audible range for some people. ID: Most calls diagnostic, but ove rlap with E. underwoodi and possibly E. perotis . Species poorly known. Active A coustic Indistinguishable from Eumops in flight. Tadarida brasiliensis Brazilian free tailed bat 2 1 1 1 Capture: While sometimes captured in mist nets, this species flies high and is generally more abundant than net captures woul d suggest. ID: Generally distinctive, but potentially confused with N. femorosaccus. Roost Location: Highly colonial and easy to detect in man made roosts; difficult in most natural roosts. Natural roosts (e.g., cliff roosts) dominate in large portion of range. Commonly in man mad e roosts in portion of its range. ID: Easy to locate and ID in most roosts. Guano and odor distinctive. Passive acoustic Detection: Easy to detect acoustically. ID: Some calls overlap with other species ( Lasionycteris , Eptesicus , L. cinereus , N. femorosac cus ), but fair proportion are diagnostic. In most settings this would be the easiest way to detect the species. Active Acoustic Visually distinctive except where overlaps with N. femorosaccus .

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© 2011 Bat Conservation International Page 207 The Durango Workshop and its Role in the Developmen t of a Western Bat Survey Protocol A standard bat survey protocol has been recognized as an essential tool to further understanding of the distribution of bat s pecies in western North America. In 2002, the Western Bat Working Group (WBWG), in collabora tion with biologists at the USDA Forest Service Redwood Sciences Laboratory in Arcata, California formed a steering committee (see list of members, below) to plan the development and publication of a handbook that would provide reco mmendations for biologis ts with adequate training and experience in bat detection methods to survey bats in an area of interest. Specifically, the protocol will serve the following needs: 1. To determine the presence of individual species in a survey area. 2. To use the presence data to characterize the species composition in a survey area. 3. To contribute information useful for the design and implementation of regional, national, and range wide monitoring strategies. There have been a number of very useful guides produced that meet some of the bat survey information needs perceived by the committee, and the scientific literature has made clear the challenges of surveying and monitoring bat populations. However, the committee determined that no existing document provides the instruct ions necessary to achieve consistent collection of the data on the occurrence of individual bat species throughout their rang es in western North America. This need is the primary motivation for the development of a comprehensive survey manual. The commi ttee recognized that an excellent source of information on effective survey methods for individual species resides in the col lective experience of field biologists that participate in the WBWG. Thus, on February 1, 2003 the WBWG steering committee organiz ed a one day workshop in Durango, Colorado (associated with the Four Corners/WBWG meeting) to formally solicit the opinions of all who were willing to volunteer information. The goal was to cap ture the expertise of field biologists who had familiarity wit h bats in one or more roost habitat groups: (1) Cave roosting bats, (2) Tree roosting bats, (3) Cliff roosting bats, and (4) Bats that roost in multiple habitats. Prior to the meeting, the steering committee produced a draft version of a spreadsheet that provided a suggested value for the utility of each of 4 survey methods for all bat species in each habitat group. The methods included: (1) net capture, (2) roost survey, (3) passive acoustic, an d (4) active acoustic. Active and passive were distinguishe d by whether behavioral or morphological information is observed and recorded during the collection of a vocalization. All 33 bat species that occur in the western U.S. and Canada were considered. The possible values for each method, for each species, w ere: 1 = preferred or highly effective; 2 = effective in most habitats; 3 = effective in some habitats; 4 = presents serious challenges; 5 = generally not effective; U = unknown. The suggested va lue that appeared in each cell of the matrix was included as a starting point for discussion; each group was asked to achieve a consensus opinion about a final value for each cell. T he final value could (and often did) differ from the original, suggested value. Each group was facilitated by an individual who wa s instructed to solicit the opinions of all participants and who recorded important discussion topics. Each group then reported back to all workshop participants and additional comments were recorde d. After the meeting, the steering committee generated a revised matrix. View the final version of the bat survey matrix by clicking on the highlighted text. This document reflects, to the best of opinions of the approximately 70 participants at the workshop. The matr ix is primarily intended as a resource to be used by those who will be developing the text of a bat survey protocol. Importantly, the matrix is not a survey protocol. It is one of a number of sources of information that wil l be used to generate a survey protocol. In the interim, however, we expect that it will be a useful reference for people who are interested in the conventional wisdom about the value of different survey methods for each species. The final protocol that the committee envisions will be much more than a simple matrix of recommended methods; it will be a comprehensive, peer reviewed, collection of recommended, standardized procedures to meet various bat survey objectives. It will be a handbook fo r field biologists that will assist their training in the use of survey methods and provide guidelines for the spatial and temporal allocation of survey effort. The committee looks forward to taking the next steps toward the development of this protocol and thanks everyone who was will ing to spe nd an extra day in Durango to share their expertise. Comments on any aspect of the matrix may be directed to Ted Weller: WBWG Steering Committee Members: Lisa Wilkinson (chair), Linda Angerer, Mary Kay Clark, Michael Herder , Lyle Lewi s, Pat Ormsbee, Dixie Pierson USDA Forest Service, Redwood Science Laboratory Staff: Ted Weller, Bill Zielinski


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