Antrozous pallidus

Although Antrozous koopmani of Cuba is treated as a separate species by ASM (2025) and Simmons and Cirranello (2025), both sources state that additional research is needed. It is possibly extinct and only known from a few modern and fossil representatives.

Large range in western North America; in some areas, habitat has been reduced and degraded by agricultural expansion, cheatgrass invasion, fire, urban development, excessive livestock grazing, and pesticide use, but the species remains widespread, common, and likely relatively stable in many areas of the arid southwestern United States; however, regional population trends are poorly known.

Range includes western North America from south-central British Columbia (Okanagan Valley; small resident population; Willis and Bast 2000; Rambaldini and Brigham 2008, 2011) south through the western United States to southern Baja California, central Mexico, southern Kansas, and southern Texas; also Cuba (Martin and Schmidly 1982, Hermanson and O'Shea 1983, Reid 2006). Elevational range in Texas is 600-2,000 meters (Ammerman et al. 2012).

The following subspecies distributions are from Martin and Schmidly (1982). Subspecies pacificus: Pacific Coast Ranges of western Oregon and California south to Los Angeles and San Bernardino counties. Subspecies pallidus: east of the range of pacificus from southern British Columbia and east of the Cascade Range throughout much of the Columbia Plateau and Great Basin, throughout the southwestern U.S.. west of central Texas, and south to western and south-central Mexico north of the Transverse Volcanic Cordillera. Subspecies bunkeri: Barber County, Kansas, south to the western end of the Wichita Mountains in Greer County, Oklahoma. Subspecies minor: s. Baja California north through the Colorado Desert of southeastern California and southwestern Arizona, thence northward into southern Nevada. Subspecies packardi: western slopes of the Sierra Madre Occidental in southwestern Zacatecas, Jalisco, northeastern Nayarit, and southern Sonora. Subspecies koopmani: several scattered localities in Cuba.

The number of distinct occurrences has not been determined using standardized criteria, but this species is represented by a large number of collection/observation sites and locations (as defined by IUCN).

On a range-wide basis, no major threats are known. Locally, some maternity colonies and hibernacula are susceptible to disturbance, and they may be negatively affected or destroyed as a result of vandalism, mine closures or reactivation, or other activities. Tree-roosting populations (Baker et al. 2008) may be detrimentally affected by timber harvest and other forestry practices. Roosts in buildings may be lost as a result of demolition, bat exclusion, or other alterations. Some populations undoubtedly have been negatively affected by loss or extensive modification of primary foraging habitat caused by agricultural expansion (including orchards and vineyards), cheatgrass invasion, fire, urban development, excessive livestock grazing, and pesticide use (Willis and Bast 2000), but the degree of impact of these threats on the affected populations is not well known.

Apparent declines in lowland south-coastal California likely are associated with loss of habitat primarily due to urban expansion (Miner and Stokes 2005).

The species undoubtedly has lost considerable habitat in Washington because of agricultural expansion (Hayes and Wiles 2013).

As of mid-2012, this species was not known to be affected by white-nose syndrome.