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MAMMALS
Western Red Bat (Lasiurus blossevillii)
Western Red Bat
(Lasiurus blossevillii)
Legal Status
State: Species of Special Concern
Federal: None
Critical Habitat: N/A
Recovery Planning: N/A
Photo courtesy of Merlin D. Tuttle, Bat
Conservation International, www.batcon.org.
Taxonomy
The western red bat (Lasiurus blossevillii) was formerly considered a
subspecies of the red bat (L. borealis); i.e., L. borealis teliotis. The
western red bat was split from the eastern red bat (which retained the
borealis species epithet), based on genetic work by Baker et al. (1988).
Using protein electrophoresis, Baker et al. (1988) found a “genetic
demarcation” between red bat samples from Texas, South Carolina,
and Georgia and those from New Mexico, Mexico, and Venezuela.
Based these data, Baker et al. (1988) concluded that the western
U.S./Southern American samples represented a distinct species from
the eastern United States species. This supported earlier
morphometric work by Schmidly and Hendricks (1984, as cited in
Baker et al. 1988) indicating physical distinctions between eastern
and western red bats in size (eastern red bats being larger) and
pelage (western red bats having more reddish fur vs. more brownish
fur in eastern red bats). Morales and Bickham (1995) confirmed the
genetic distinction between the western and eastern red bat species
using mitochondrial DNA analysis.
Subspecies distinctions for the western red bat are still uncertain.
Currently, four subspecies are recognized: L. b. teliotis, L. b. frantzii, L.
b. blossevillii, and L. b. brachyotis (Wilson and Reeder 2005). Baker et
al. (1988) suggested that western red bat samples in their study
represented two subspecies based on the samples analyzed from New
Mexico, Mexico, and Venezuela: L. b. teliotis and L. b. frantzii. L. b.
teliotis occurs in the western United States and Mexico, while L. b.
frantzii occurs in Central and South America. However, Morales and
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Western Red Bat (Lasiurus blossevillii)
Bickham (1995) found no genetic difference between L. b. teliotis and
L. b. frantzii from Belize in Central America, indicating that this
distinction is misleading or could represent genetic exchange between
these two subspecies. They recommended that the western United
States, Mexico and Central American populations be assigned to the
subspecies L. b. frantzii and that the South American subspecies L. b.
blossevillii could be recognized as a separate species based on genetic
differences. L. b. brachyotis is endemic to the Galapagos Islands.
However, as noted previously, the four subspecies listed are still in
place (Wilson and Reeder 2005). Despite the uncertainty about the
western red bat subspecies, the full western red bat species is
designated a California Species of Special Concern (CDFG 2011a), so
these taxonomic issues are not critical to the Desert Renewable
Energy Conservation Plan (DRECP).
A physical description for red bats is provided by Shump and Shump
(1982). However, this description was written for the red bat before
the western red bat was split from the eastern red bat. Schmidly and
Hendricks (1984, as cited in Baker et al. 1988) noted that western
populations were smaller than eastern populations and had rusty-red
dorsal fur compared to the more brown dorsal coloration in the
eastern red bat.
Distribution
General
The western red bat occurs in southern British Columbia, the western
United States, Mexico, Central Mexico, and possibly South America
(Cryan 2003; Pierson et al. 2006) (Figure SP-M10). Cryan (2003)
suggests that there may be areas of overlap with the eastern red bat in
western Texas, New Mexico, and Mexico. Although the species has a
wide range, relatively few records for the western red bat exist
outside of California (Pierson et al. 2006). In California, most of the
records are from the Central Valley, which is the breeding center for
the western red bat in the state. About 83% of the breeding records
for western red bat in California are from the Sacramento and San
Joaquin rivers, with other breeding records from the San Diego, Santa
Ana, and Los Angeles rivers (Pierson et al. 2006).
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Western Red Bat (Lasiurus blossevillii)
Although the Central Valley is the center of activity during the
reproductive season (May through August), western red bats occur
throughout low elevations of California. Individuals appear to stay in
California year-round because there are occurrence records for every
month of the year (Pierson et al. 2004). There is evidence for seasonal
movements by western red bats in California, but little evidence for
mass migrations characteristic of the eastern red bat and other tree
bats such as the hoary bat (Lasiurus cinereus) (Cryan 2003; Pierson et
al. 2006). The northern extent of the species’ summer range in
California appears to be Humboldt County. Kennedy (2011) recorded
the first occurrences of western red bat in the redwood forest in
Humboldt County about 50 kilometers (31 miles) north of the species’
suspected range, but only two calls were detected in almost 18
months of continuous recording, indicating its rarity in the area.
The distributions of males and females in California differ seasonally.
Males are dispersed throughout the state during the reproductive
season, while females are concentrated in the Central Valley (Pierson
et al. 2006). During the non-reproductive season, both males and
females in California are more dispersed, with 54% of the records
along the coast south of Humboldt County, 24% in the Central Valley,
and 21% in Southern California (Pierson et al. 2006). Winter records
are mostly from areas that rarely freeze. Most records are from
elevations below 200 meters (656 feet) (Pierson et al. 2006). There
are scattered records for the western Sierra Nevada foothills, and
records from higher elevations (a maximum of 2,484 meters [8,150
feet]) are most likely for males (Pierson et al. 2006).
Distribution and Occurrences within the Plan Area
Historical
There are very few records for western red bat in the desert regions
of California. Pierson et al. (2006) report two records for Death Valley,
one in the Bishop area of the Owens Valley, a breeding record for the
Twentynine Palms area, and one in Nevada, east of the White
Mountains. There are no historical (i.e., pre-1990) California Natural
Diversity Database (CNDDB) records for the western red bat in the
Plan Area (CDFG 2011b).
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Western Red Bat (Lasiurus blossevillii)
Recent
There are no recent (i.e., since 1990) CNDDB (CDFG 2011b) or other
records for western red bat in the Plan Area.
Natural History
Habitat Requirements
The western red bat, as a tree bat, is closely associated with welldeveloped riparian habitats that provide suitable roosting sites.
Pierson et al. (2006) conducted acoustic and selected mist netting
surveys at potential roosting sites in the Central Valley. Most of the
sample locations were along the Sacramento and San Joaquin rivers,
as well as tributaries and some other selected sites with suitable
habitat. At each site they assigned the riparian habitat to one of three
categories: (A) Fremont cottonwood (Populus fremontii)/western
sycamore (Platanus racemosa) and/or valley oak (Quercus lobata) in
zones at least 50 meters (164 feet) wide; (B) mature trees but only
two or three trees wide; and (C) one tree and secondary
growth/young trees in sparsely vegetated riparian strips. They also
had a fourth non-riparian category: (D) grass/shrubs more than 100
meters (328 feet) to nearest trees. Western red bats were detected
wherever there was suitable riparian habitat, but most of the
detections were in the “A” category. Pierson et al. (2006) also
observed foraging along gravel bars within rivers, but only where the
gravel bars were at least 50 meters (164 feet) wide and several
hundred meters long. Notably, western red bat densities peaked in
July and August and then declined in the fall, presumably when bats
were moving to winter sites.
Along the lower Colorado River, cottonwood-willow (Salix spp.)
riparian habitat and honey mesquite (Prosopis glandulosa) are
considered suitable roosting and foraging habitats for migrating and
potentially year-round residents in the area (Lower Colorado River
Multi-Species Conservation Program (LCR MSCP 2004); however, no
western red bat records exist for the LCR MSCP planning area.
Although Pierson et al. (2006) determined that western red bats
differentially select wide, well-developed riparian habitats with
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Western Red Bat (Lasiurus blossevillii)
mature trees (i.e., A-category habitats) over more narrow zones and
young trees for breeding roosts (i.e., B- and C-category habitats), the
species frequently has been observed using non-native trees for
roosting. Western red bats have been observed in orchard trees,
including fig (Ficus carica), apricot (Prunus armeniaca), peach (Prunus
persica), pear (Pyrus communis), almond (Prunus amygdalus), walnut
(Juglans regia), and orange trees (Citrus sinensis) (Benson 1945, as
cited in Pierson et al. 2006; Constantine 1959; Grinnell 1918, as cited
in Pierson et al. 2006; Pierson et al. 2006). They have also been
observed to use other non-native trees, including African hemp
(Sparmannia Africana), eucalyptus (Eucalyptus spp.), Chinaberry
(Melia azedarach), mulberry (Morus rubra), and tamarisk (Tamarix
spp.)(Constantine 1959; Dalquest, as cited in Pierson et al. 2006;
Grinnell 1918, as cited in Pierson et al. 2006; Orr 1950; Pierson et al.
2006). The use of orchards and potential exposure to pesticides is
discussed in Threats and Environmental Stressors.
There is little information about roost site characteristics favored by
the western red bat (e.g., microclimates, cover density, tree aspect)
because most of the ecological studies have been carried out in the
east within the range of the eastern red bat. Pierson et al. (2006)
hypothesize that western red bats roost in the canopy of the largest
trees, based on data for eastern red bats, but note that western red bat
habitat associations are very different from the more common eastern
red bat.
Tree roosting bats in general are more exposed to ambient
temperatures than cave, rock, and mine dwelling species; therefore,
physical, physiological, and/or behavioral adaptations to more
extreme conditions would be expected. Davis and Lidicker (1956)
reported that eastern red bats hibernate, but this adaptation to cold
temperatures may not apply to western red bat. However, like eastern
red bats, western red bats have thick fur and rounded ears, which
indicate adaptations to cold conditions.
Based on the apparent habitat requirements of western red bats for
breeding and the fact that the vast majority of breeding records for
the species are in the Central Valley, it is unlikely that western red bat
breeds in much of the Plan Area. However, it may be a resident in the
lower Colorado River area (LCR MSCP 2004). The species may also
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Western Red Bat (Lasiurus blossevillii)
winter in suitable riparian habitats in the Plan Area, particularly along
the lower Colorado River. Potential habitats supporting the western
red bat in the Plan Area are listed in Table 1.
Table 1. Habitat Associations for Western Red Bat
Land Cover Type
Forest, woodland,
riparian, mesquite
bosque
Habitat
Designation
Winter
roosting,
foraging
Habitat
Parameters
Forest, woodland,
riparian, mesquite
bosque
Supporting
Information
Pierson et al.
2006, LCR MSCP
2004
Foraging Requirements
The foraging information provided in this section is for the red bat, as
summarized by Shump and Shump (1982) prior to its split into two
species, and mostly reflects data for eastern populations. It is assumed
for the purpose of this profile that the information is generally
applicable to the western red bat. Red bats appear to select prey by size
rather than taxonomic groups (e.g., in contrast to bats that are moth
specialists). They feed on a variety of prey, including Lepidoptera
(moths), Homoptera (e.g., cicadas, leaf hoppers), Coleoptera (beetles),
Hymenoptera (wasps), Diptera (flies), and Orthoptera (crickets,
grasshoppers) (Shump and Shump 1982). Red bats usually emerge to
forage 1 to 2 hours after sunset and may forage for several hours
during a primary foraging bout, and again later in the night during a
secondary bout. LaVal and LaVal (1979) reported late afternoon
foraging activity in Missouri, but this activity appears to be uncommon
even though it has also been reported by others (Davis and Lidicker
1956; Barbour and Davis 1969 and Whitaker and Mumford 1972, as
cited in La Val and LeVal 1979). Their foraging activity may be timed in
relation to the foraging behavior of other bat species and the early
nocturnal activity of their insect prey (see Ecological Relationships).
Red bats appear to forage in the same areas over time, but there is little
information about spatial foraging patterns.
Red bats become active at temperatures of about 20 degrees Celsius
(68 degrees Fahrenheit), but have been observed flying at
temperatures as low as 7 degrees Celsius (44.6 degrees Fahrenheit)
(LaVal and LaVal 1979; Shump and Shump 1982). LaVal and LaVal
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Western Red Bat (Lasiurus blossevillii)
(1979) observed red bats in Louisiana and Missouri foraging in a
variety of habitats, including along streams and rivers, gravel bars,
riparian areas, floodplains, and hill forests. Pierson et al. (2006) also
observed western red bats flying along wide gravel bars in California.
They are often observed feeding in large numbers at lights that attract
insects (e.g., LeVal and LeVal 1979).
Reproduction
As with foraging requirements, information about reproduction is
primarily for the red bat, and may be somewhat different for the
western red bat in association with their different ecological setting
and potentially different seasonal activity patterns. Breeding occurs in
August and September (Shump and Shump 1982). Females store the
sperm, and fertilization occurs in the spring. Gestation is estimated to
be 80 to 90 days. Litter sizes are relatively large for bats (as is
characteristic of solitary tree bats compared to colonial bats), with an
average of about 2.3 young, and litters as large as 5 young (Hamilton
and Stalling 1972; LaVal and LaVal 1979; Shump and Shump 1982).
The young are relatively undeveloped at birth; they are hairless and
their eyes are closed. They are weaned by 4 to 6 weeks and fly
between 3 and 6 weeks (Shump and Shump 1982).
Key seasonal periods for western red bat are summarized in Table 2.
7
Sep
Oct
Nov
Dec
Reproduction
x
x
x
Seasonal
Movements/
Wintering
x
x
x
x
________________
Notes: There is no evidence for mass migration.
Sources: Pierson et al. 2006; Cryan 2003.
Aug
July
June
May
April
March
Feb
Jan
Table 2. Key Seasonal Periods for Western Red Bat
x
x
x
x
x
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Western Red Bat (Lasiurus blossevillii)
Spatial Activity
As described previously under Distribution, western red bats appear
to make seasonal movements in California, but there is little evidence
for mass migrations (Cryan 2003; Pierson et al. 2006). Breeding
females appear to leave summer sites by September (Pierson et al.
2006), the time period in which males and females come together for
breeding. As noted under Distribution, males are much more
dispersed in California during the spring/summer reproductive
season. How far individual western red bats move is unknown, but it
is expected to be at least several hundred miles given that populations
in southern and coastal California expand in the winter; presumably
individuals moving to southern California include females that breed
in the Central Valley. In addition, western red bats have a relatively
low wing load and are relatively fast fliers (Shump and Shump 1982);
therefore, seasonal movement of several hundred miles is plausible.
No information is available for spatial patterns related to foraging
activities (e.g., what are nightly flight distances, do they exhibit
centers-of-activity, and do they spatially partition foraging areas with
other bat species?). Pierson et al. (2006) observed western red bat
activity over wide gravel bars and along the edges of riparian habitat,
but little activity over “denuded” river banks (i.e., grass or riprap).
Pierson et al. (2006) recommend radiotelemetry studies of this
species to better understand its behavior, especially with regard to
conservation and management activities.
Ecological Relationships
Pierson et al. (2006) recorded up to 13 other bat species at sites
where western red bats were documented in the Central Valley (see
Table 3 in Pierson et al. 2006). This high diversity of bats indicates
that the well-developed riparian habitats used by western red bats
are also high value habitat for other species, including roosting habitat
for other tree bats such as silver-haired bat (Lasionycteris
noctivagans) and hoary bat, and foraging habitat for other
insectivorous bats. Western red bat usually was not the most
abundant species at sites, but it was one of the most widely
encountered across the habitats sampled by Pierson et al. (2006),
exceeded only by the Mexican free-tailed bat (Tadarida brasiliensis).
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Western Red Bat (Lasiurus blossevillii)
Black (1974) suggested that bats may employ several types of foraging
and food partitioning mechanisms that could reduce inter-specific
competition, including size and type of prey; periods of activity (most
bat prey are active within a few hours of sunset, but different prey have
different peak activity periods); spatial partitioning, such as between-,
within-, and below-canopy foragers; and flight patterns, such as slow
vs. fast flying, maneuverability, and hovering.
At one site, Pierson et al. (2006) observed initial, intense foraging by
big brown bat (Eptesicus fuscus) and a Myotis species, followed 15
minutes later by western red bats as the dominant species, appearing
suddenly from the tree canopy. Otherwise, the Pierson et al. (2006)
study did not address temporal or other potential resource
partitioning strategies among the different bat species.
Kunz (1973) found temporal associations between red bat and other
bats in Iowa, with the red bat foraging in the earliest period (1-2
hours after sunset), followed by silver-haired bat (3-4 hours after
sunset), and hoary bat (4-5 hours after sunset). Kunz (1973)
suggested that earlier activity of red bats was correlated with the
activity of a variety of insect prey and the later activity of hoary bats
corresponded to the availability of moths, its preferred prey. Kunz
(1973) also noted spatial separation of red bats and hoary bats; where
red bats are common, hoary bats are less common, and vice versa.
Whether these kinds of resource partitioning mechanisms apply to
the bat communities in California is unknown.
As noted previously in Foraging Requirements, red bats are often
observed foraging at artificial lights. Artificial lighting may affect
competitive predator-prey relationships among bats. Longcore and
Rich (2004) suggest that artificial lighting, which attracts many
insects taken by bats, including moths (Frank 1988), may alter local
community relationships because the faster-flying bats congregate
around lights and can exploit this concentrated food source while
slower-flying bats avoid lights and are unable to benefit from this
concentration of insects. Hickey et al. (1996) found that red bats and
hoary bats foraging at the same street lights at a site in Ontario,
Canada, take prey of different size classes, with the smaller red bat
(half the size of the hoary bat) taking smaller prey, indicating possible
resource partitioning at these artificial foraging sites.
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Western Red Bat (Lasiurus blossevillii)
Population Status and Trends
Global: Secure (NatureServe 2011)
State: Vulnerable (?) (CDFG 2011a)
Within Plan Area: Unknown
Western red bat is a California Species of Special Concern, but its
population status and trends within its range in the western United
States and within California are unknown. However, Pierson et al.
(2006) noted that there were relatively few, scattered records for the
species outside of California. Their review found only two records for
British Columbia, Canada, none for Washington and Oregon, four for
Utah, and less that 12 each for Arizona and New Mexico. Based on a
recommendation by Pierson et al. (2006), the western red bat was
designated a California Species of Special Concern. This
recommendation was based on the fact that the western red bat was
split from the eastern red bat, elevating the concern for its
conservation within its more restricted range and limited riparian
habitats in the western United States. Additionally, the breeding
stronghold for this species in California is in the Central Valley, along
the Sacramento and San Joaquin drainages and other large rivers that
drain the Sierra Nevada (Pierson et al. 2006). The large riparian zones
within these drainages have historically been subjected to loss and
degradation, reducing high quality roosting and foraging habitat
available to the species. Nonetheless, Pierson et al. (2006) did find the
species at all suitable habitat sites in their sample area, and it does use
non-native tree species for roosting, indicating that it is not
imminently threatened, thus reflecting its designation as possibly
vulnerable in California (CDFG 2011a).
Threats and Environmental Stressors
The primary threat to western red bat is loss and degradation of welldeveloped riparian zones that support larger, mature trees such as
Fremont’s cottonwood, western sycamore, and valley oak within the
Central Valley and elsewhere along major rivers and tributaries.
Pierson et al. (2006) also express concern that pesticide use at occupied
orchards could harm western red bats, either through direct poisoning
or indirectly through impacts on prey abundance, especially if the bats
are using the orchards as compensation for the historical loss of native
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Western Red Bat (Lasiurus blossevillii)
riparian habitats (particularly walnut orchards along the Sacramento
River). Pierson et al. (2006) suggest that if pesticides adversely affect
western red bats, the orchards may function as “sink’ habitat.
Human activities may also affect roosting and reproduction, especially
if pregnant and lactating females are roosting in orchards subject to
high levels of human activity. Constantine (1959) reported that
human activities in orchards caused bats to fly from the roosts,
although they returned the next day. Human talking and walking
around roost sites did not appear to substantially disturb bats, but
any attempt to handle the bat did. It is expected that active work in
the trees such as pruning and harvesting would adversely affect
roosting individuals and potentially disrupt reproduction (e.g.,
tending of young during early development phases).
Prior to the 2000s, fewer than 200 bat fatalities due to collisions with
artificial structures had been documented (Cryan 2011). Since the late
1990s, bat fatalities, primarily related to wind energy facilities, have
dramatically increased (Cryan 2011; Kunz et al. 2007). The migratory
tree bats—red bats, hoary bats, and silver-haired bats—make up the
majority of fatalities (Arnett et al. 2005), with eastern red bat
comprising about 20% of all documented fatalities to date (Cryan
2011). The number of bat fatalities attributed to wind energy facilities
is very high, with an estimate of up to 450,000 per year (Cryan 2011).
For example, between 1,500 and 4,000 bats were estimated to have
died at a single wind energy site during 2004 (Cryan 2011). However,
fatality rates are highly variable, and estimates for individual wind
facility sites have ranged from just below one bat per installed
megawatt per year (bats/MW/yr) to as high as 70 bats/MW/yr
(Cryan 2011). The highest bat fatalities appear to occur where
facilities are built on ridge tops (Johnson and Erickson 2008).
In the western United States in Washington and Oregon, bat fatalities
at wind energy facilities have been similar to other parts of the
country. Bat fatality estimates for the Columbia Plateau Ecoregion
(CPE) were made for 10 existing wind facilities and ranged from 0.39
to 2.46 fatalities/MW/yr, with an average of 1.18 fatalities/MW/yr
(Johnson and Erickson 2008). However, no fatalities of western red
bats were documented in this study even though the CPE is within the
range of the species.
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Western Red Bat (Lasiurus blossevillii)
Red bat fatalities from collisions with tall buildings in New York and
Chicago (Terres 1956; Timm 1989, as cited in Cryan 2011) and a
television tower in Kansas (Van Gelder 1956, as cited in Cryan 2011)
have also been documented.
Cryan (2011) suggests that there may be something about the
behavior of tree bats that makes them more vulnerable to collisions,
such as the seasonality and pattern of migrations. Johnson and
Erickson (2008) assume that the hoary bat fatalities in the CPE are of
individuals migrating from breeding habitat in the surrounding
mountainous/forested ecoregions or from more northern areas in
Canada, but that the dynamics of these populations would need to be
known to predict population effects. As noted above, no fatalities of
western red bats have been documented in the CPE.
Conservation and Management Activities
The western red bat is a Covered Species under the LCR MSCP (2004).
Although the species has not been recorded in the LCR MSCP planning
area, it is thought to migrate through the area and may be a yearround resident (see Appendix I, Status of LCR MSCP Covered Species,
in LCR MSCP 2004). The LCR MSCP identifies cottonwood-willow
habitat and honey mesquite as suitable roosting and foraging habitat
for western red bat. One of the conservation measures in the LCR
MSCP is to provide replacement riparian habitat that would benefit
western red bat, including removal of tamarisk and replacement with
suitable native habitat. The LCR MSCP conservation goal for western
red bat is to create 765 acres of roosting habitat, defined as
cottonwood-willow and honey mesquite. In addition, this habitat will
be monitored and managed, and surveys for western red bat will be
conducted to identify habitat requirements and the species’
distribution in the MSCP area.
Data Characterization
There are virtually no current data for western regarding its
distribution and habitat use in the Plan Area, including seasonal
movements and roosting sites. Because it is expected to migrate
through the lower Colorado River area and possibly be a year-round
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Western Red Bat (Lasiurus blossevillii)
resident, the LCR MSCP (2004) provides coverage for the species and
identifies suitable habitat as cottonwood-willow and honey mesquite.
Management and Monitoring Considerations
The main management consideration for western red bat is
maintaining large, wide riparian zones (i.e., greater than 50 meters
[164 feet] wide) with mature trees (e.g., cottonwoods in desert regions)
(Pierson et al. 2006). Pesticide use in agricultural areas adjacent to
suitable roosting and foraging areas should be managed to prevent
direct poisoning and secondary impacts on prey. Human activities near
active roosting sites should be curtailed to prevent disturbance.
Predicted Species Distribution in Plan Area
Modeled suitable habitat included the riparian community in the Plan
Area. There are 75,262 acres of modeled suitable habitat for western
red bat in the Plan Area. Appendix C includes specific model
parameters and a figure showing the modeled suitable habitat in the
Plan Area. Species model summary and results will be provided
following model development.
Literature Cited
Arnett, E.B., W.P. Erickson, J. Kerns, and J. Horn. 2005. Relationships
between Bats and Wind Turbines in Pennsylvania and West
Virginia: An Assessment of Fatality Search Protocols, Patterns
of Fatality, and Behavioral Interactions with Wind Turbines.
Final report prepared for the Bats and Wind Energy
Cooperative. June 2005.
Baker, R.J., J.C. Patton, H.H. Genoways, and J.W. Bickham. 1988. “Genic
Studies of Lasiurus (Chiroptera: Vespertilionidae).”Occasional
Papers, The Museum, Texas Tech University 117:1–15
Black, H.L. 1974. “A North Temperate Bat Community: Structure and
Prey Populations.” Journal of Mammalogy 55(1):138–157.
CDFG (California Department of Fish and Game). 2011a. “Special Animals
(898 taxa).” California Natural Diversity Database. CDFG,
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Western Red Bat (Lasiurus blossevillii)
Biogeographic Data Branch. January 2011. Accessed November
21, 2011.
CDFG). 2011b. “Lasiurus blossevillii.” Element Occurrence Query.
California Natural Diversity Database (CNDDB) species.
RareFind, Version 4.0 (Commercial Subscription). Sacramento,
California: California Department of Fish and Game,
Biogeographic Data Branch. Accessed December 2011.
http://www.dfg.ca.gov/biogeodata/cnddb/ mapsanddata.asp.
Constantine, D.G. 1959. “Ecological Observations on Lasiurine Bats in
the North Bay Area of California.” Journal of Mammalogy
40:131–15.
Cryan, P.M. 2003. “Seasonal Distribution of Migratory Tree Bats
(Lasiurus and Lasionycteris) in North America.” Journal of
Mammalogy 84(2):579–593.
Cryan, P.M. 2011. “Wind Turbines as Landscape Impediments to the
Migratory Connectivity of Bats.” Environmental Law 41:355-370.
Davis, W.H., and W.Z. Lidicker Jr. 1956. “Winter Range of the Red Bat,
Lasiurus borealis.” Journal of Mammalogy 37(2):280–281.
Frank, K.D. 1988. “Impact of Outdoor Lighting on Moths: An
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