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Candidate models using all parameter combinations were constructed to assess ability of landscape variables to predict presence of RBEB and SEM.
During winter, mean DBH of trees with cavities where RBEB and SEM were detected were about 1.7 and 1.4 times larger than DBH of trees with cavities where RBEB and SEM were not detected, respectively (Table 2).
In winter, RBEB and SEM occurred in cavities about 3 and 4.6 times larger than cavities without RBEB and SEM, respectively.
During winter, RBEB and SEM were located in 21 and 19 roosts, respectively.
Green Tree Reservoirs at NNWR were moderate probability use areas for RBEB and SEM (Fig.
Cavity trees with >75 cm DBH were most often used by both RBEB and SEM similar to previous studies (Mirowsky and Horner, 1997; Trousdale and Beckett, 2005; Carver and Ashley, 2008).
Area of cavity opening did not influence presence of either RBEB or SEM during either season, similar to other studies (Carver and Ashley, 2008; Gooding and Langford, 2004).
Larger tree size was associated with lower elevations; past protection of trees within streamside corridors can influence forest stand characteristics and suitability for forest dwelling bats, such as SEM and RBEB (Clark, 2000).
Elevations within floodplain forests of NNWR where most RBEB and SEM were detected in roost trees ranged from 200-235 m whereas unoccupied roosts ranged from 200-533 m.
Clark (2000) reported a similar response of RBEB to disturbance associated with forest management activities.
Green Tree Reservoirs at NNWR were moderately selected areas for both RBEB and SEM (Fig.
TABLE 1.--Seasonal occupancy, detection probability, number of surveys, and number of trees surveyed for Rafinesque's big-eared bat (RBEB) and southeastern myotis (SEM) in bottomland and riparian hardwood forests, Mississippi, 2009-2010 Detection No.
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