Values for area of occupied habitat by each species were obtained as the predicted occupied proportion of each 900 square meter pixel (i.e., occupancy probability x 900) for all habitats, except permanent water, within the Mississippi Alluvial Valley Bird Conservation Region.

Values for predicted probabilities of avian species occupancy were determined using colonization-extinction models (MacKenzie and others, 2003) as implemented in R (Version 3.4.4; https://www.r-project.org/) via the ‘colext’ function of the Unmarked package (Version 0.12-0; Fiske and Chandler 2011). Performance of a null model (without covariates) and 153 additional models that assessed the effects of geographic coordinates and habitat context covariates were evaluated using Akaike information criteria (AIC; Burnham and Anderson, 2002). When more than one model had substantial support, their respective model weights were used to spatially predict occupancy relative to covariate influence. Predictive model covariates and weights are provided in Appendix 4 (Twedt and Mini, 2020).

Values for predicted probabilities of avian species occupancy were determined using colonization-extinction models (MacKenzie and others, 2003) as implemented in R (Version 3.4.4; https://www.r-project.org/) via the ‘colext’ function of the Unmarked package (Version 0.12-0; Fiske and Chandler 2011). Performance of a null model (without covariates) and 153 additional models that assessed the effects of geographic coordinates and habitat context covariates were evaluated using Akaike information criteria (AIC; Burnham and Anderson, 2002). When more than one model had substantial support, their respective model weights were used to spatially predict occupancy relative to covariate influence. Predictive model covariates and weights are provided in Appendix 4 (Twedt and Mini, 2020).

Values for area of all occupied habitat were only obtained for species whose occupancy models predicted a marked proportion of the species' population was likely present in non-forest habitats.

Values for area of all occupied habitat were only obtained for species whose occupancy models predicted a marked proportion of the species' population was likely present in non-forest habitats.

Values for area of sustainable forest habitat for each species were obtained as the predicted occupied proportion of each 900 square meter pixel (i.e., occupancy probability x 900) within all forest patches deemed large enough to harbor a sustainable population of the species. The area required for a sustainable population of each species was derived from credible intervals associated with population trends from historical (1966-2015) BBS data (Sauer and others, 2017). For each silvicolous bird species in the Mississippi Alluvial Valley, we assumed the minimum sustainable population was the number of birds needed to ensure ≤1% probability that the population would be extirpated (i.e., drop below a quasi-extinction threshold) during a 100-year period wherein annual population change was randomly selected from the credible interval associated with each species’ population trend. We used the mean of 500 simulation replicates conducted in R (Version 3.4.4; https://www.r-project.org/) as the presumed minimum sustainable population for each species. We arbitrarily set the quasi-extinction threshold at 25 breeding pairs. Because species with credible intervals associated with their trend estimates that were inclusively positive never declined in population, by default these species had a minimum sustainable population of 25 pairs.

Values for area of sustainable forest habitat for each species were obtained as the predicted occupied proportion of each 900 square meter pixel (i.e., occupancy probability x 900) within all forest patches deemed large enough to harbor a sustainable population of the species. The area required for a sustainable population of each species was derived from credible intervals associated with population trends from historical (1966-2015) BBS data (Sauer and others, 2017). For each silvicolous bird species in the Mississippi Alluvial Valley, we assumed the minimum sustainable population was the number of birds needed to ensure ≤1% probability that the population would be extirpated (i.e., drop below a quasi-extinction threshold) during a 100-year period wherein annual population change was randomly selected from the credible interval associated with each species’ population trend. We used the mean of 500 simulation replicates conducted in R (Version 3.4.4; https://www.r-project.org/) as the presumed minimum sustainable population for each species. We arbitrarily set the quasi-extinction threshold at 25 breeding pairs. Because species with credible intervals associated with their trend estimates that were inclusively positive never declined in population, by default these species had a minimum sustainable population of 25 pairs.

This is a raster file with predicted densities of male golden-cheeked warblers as depicted in Figure 6 of Sesnie et al. (2016). The resolution is 10x10m pixels. The predicted densities are based on relationships with canopy cover, proportion of canopy composed of juniper, and annual solar radiation.

This is a raster file with predicted densities of male golden-cheeked warblers as depicted in Figure 6 of Sesnie et al. (2016). The resolution is 10x10m pixels. The predicted densities are based on relationships with canopy cover, proportion of canopy composed of juniper, and annual solar radiation.

This dataset includes information on detections of Bachman's Sparrow, Northern Bobwhite, and Red-cockaded Woodpecker at 161 locations in Georgia, USA. In addition to detections of birds and corresponding detection covariates (date, time, temperature, and observer), habitat metrics derived from satellite imagery and on-the-ground vegetation measurements are included.