We investigated fine-scale genetic patterns of the federally threatened Eastern Massasauga Rattlesnake (Sistrurus catenatus) on a relatively undisturbed island in northern Michigan, USA. This species often persists in habitat islands throughout much of its distribution due to extensive habitat loss and distance-limited dispersal. These data are from 102 individual Eastern Massasauga Rattlesnakes sampled at Bois Blanc Island, Michigan and genotyped at 15 microsatellite loci. Samples were collected as part of a study to examine functional connectivity for the Eastern Massasauga. We found that the entire island population exhibited weak genetic structuring with spatially segregated variation in effective migration and genetic diversity.

We collected ddRADseq data using the Peterson et al. 2012 (see Methodology for full citation) protocol to study the population structure and genetic diversity of two threatened species of gartersnakes inhabiting the lower Colorado River Basin in the United States: Mogollon Narrow-headed gartersnake (Thamnophis rufipunctatus) and Northern Mexican gartersnake (T. eques megalops). Data were sequenced on an Illumina HiSeq 2500 and 4000 to generate 50 base pair sequence reads and stored as fastq files. Data were submitted to NCBI in an approved format for their database. Data are stored in the NCBI Sequence Read Archive in fastq file format and can be found at https://www.ncbi.nlm.nih.gov/sra/SRP144044 These data support the following publication: Wood, D.A., Emmons, I.D., Nowak, E.M., Christman, B.L., Holycross, A.T., Jennings, R.D., and Vandergast, A.G., 2018, Conservation genomics of the Mogollon Narrow-headed gartersnake (Thamnophis rufipunctatus) and Northern Mexican gartersnake (T. eques megalops): U.S. Geological Survey Open-File Report XXXXXXXXX

We compared genetic diversity and body condition indices among two source locations in Catron County, New Mexico (Whitewater Creek and Middle Fork Gila) and the recipient population (Saliz Creek) to evaluate individual- and population-level fitness responses related to the admixture of gene pools following the the translocation of Mogollon Narrow-headed Gartersnakes (Thamnophis rufipunctatus). Our body condition dataset consisted of 294 snakes, and 174 genetic samples were used for genetic diversity estimates, with 95 snakes sharing both genetic and body condition data used for heterozygosity-fitness correlation analyses. As Thamnophis rufipunctatus is listed as threatened under the Endangered Species Act, sensitive location information can be made available upon request by contacting the dataset point of contact.

The Mogollon Narrowheaded gartersnake (Thamnophis rufipunctatus) and the Northern Mexican gartersnake (Thamnophis eques megalops) are both listed as Threatened under the Federal Endangered Species Act. Both species have a strong association with aquatic habitats, and these habitats have been highly altered from impoundments, land-use changes, and the introduction and spread of non-native aquatic species, which have contributed to declines in Arizona and New Mexico over the last 30-40 years. We characterized 125 microsatellite loci per species to generate genetic toolsets for use in long term genetic monitoring of populations. We evaluated microsatellite loci for missing data and several variability thresholds, which resulted in 108 microsatellite loci for T. rufipunctatus and 91 microsatellite loci for T. eques megalops.

The Mogollon Narrowheaded gartersnake (Thamnophis rufipunctatus) and the Northern Mexican gartersnake (Thamnophis eques megalops) are both listed as Threatened under the Federal Endangered Species Act. Both species have a strong association with aquatic habitats, and these habitats have been highly altered from impoundments, land-use changes, and the introduction and spread of non-native aquatic species, which have contributed to declines in Arizona and New Mexico over the last 30-40 years. We characterized 125 microsatellite loci per species to generate genetic toolsets for use in long term genetic monitoring of populations. We evaluated microsatellite loci for missing data and several variability thresholds, which resulted in 108 microsatellite loci for T. rufipunctatus and 91 microsatellite loci for T. eques megalops.

This dataset includes location, field measurements, and descriptions of 330 Uma inornata sampled for the research study entitled “Sampling Across 20 Years (1996–2017) Reveals Loss of Diversity and Genetic Connectivity in the Coachella Valley Fringe-Toed Lizard (Uma inornata)”. Field sampling occurred between March and September of 2017 and between April and June of 2018. Lizards were located by visually searching dune habitat in all major populations. Sites included Windy Point, Willow Hole, Train Station, Whitewater, and the South Coachella Valley Preserve. In addition, satellite populations in the Indio Hills and individuals salvaged from Section 24 and translocated to Stebbin’s Dune were also sampled. Lizards were captured by hand or noose. Each individual was weighed, snout-vent length was measured, and sex, breeding and other body conditions were noted. Individuals were photographed with a standard color palette against a standard black background board. Finally, a small tail-clip was taken and stored in 95 percent ethanol for future genetic analysis. Individuals were released at the point of capture, with the exception that those collected in Section 24 were moved to Stebbins Dune.

This dataset includes location, field measurements, and descriptions of 330 Uma inornata sampled for the research study entitled “Sampling Across 20 Years (1996–2017) Reveals Loss of Diversity and Genetic Connectivity in the Coachella Valley Fringe-Toed Lizard (Uma inornata)”. Field sampling occurred between March and September of 2017 and between April and June of 2018. Lizards were located by visually searching dune habitat in all major populations. Sites included Windy Point, Willow Hole, Train Station, Whitewater, and the South Coachella Valley Preserve. In addition, satellite populations in the Indio Hills and individuals salvaged from Section 24 and translocated to Stebbin’s Dune were also sampled. Lizards were captured by hand or noose. Each individual was weighed, snout-vent length was measured, and sex, breeding and other body conditions were noted. Individuals were photographed with a standard color palette against a standard black background board. Finally, a small tail-clip was taken and stored in 95 percent ethanol for future genetic analysis. Individuals were released at the point of capture, with the exception that those collected in Section 24 were moved to Stebbins Dune.

Dataset containing information for white-tailed deer samples from Ohio, Pennsylvania, Maryland, Virginia and New York, genotyped for 11 microsatellites markers. Marker OvirQ should not be used as it presents alleles inconsistent with reported pattern, with some alleles separated by only 1 base pair and inconsistent between runs. Projected coordinates representing sampling location are in a user-defined CRS, similar to USA Contiguous Albers Equal Area Conic: "+proj=aea +lat_1=29.3 +lat_2=45.3 +lat_0=23 +lon_0=-96 +x_0=0 +y_0=0 +ellps=GRS80 +towgs84=0,0,0,0,0,0,0 +units=m +no_defs".

Dataset containing information for white-tailed deer samples from Ohio, Pennsylvania, Maryland, Virginia and New York, genotyped for 11 microsatellites markers. Marker OvirQ should not be used as it presents alleles inconsistent with reported pattern, with some alleles separated by only 1 base pair and inconsistent between runs. Projected coordinates representing sampling location are in a user-defined CRS, similar to USA Contiguous Albers Equal Area Conic: "+proj=aea +lat_1=29.3 +lat_2=45.3 +lat_0=23 +lon_0=-96 +x_0=0 +y_0=0 +ellps=GRS80 +towgs84=0,0,0,0,0,0,0 +units=m +no_defs".

Monitoring change in genetic diversity in wildlife populations across multiple scales could facilitate prioritization of conservation efforts. We used microsatellite genotypes from 7,080 previously collected genetic samples from across the greater sage-grouse (Centrocercus urophasianus) range to develop a modelling framework for estimating genetic diversity within a recently developed hierarchically nested monitoring framework (clusters). The majority of these genetic samples (n=6560) were used in previous research (Oyler-McCance et al. 2014; Cross et. al 2018; Row et. al. 2018). Genetic diversity values associated with clusters across multiple scales could facilitate the identification of areas with low genetic diversity and inform the potential management or conservation priority and response. We also report the data used to define genetic diversity thresholds of conservation concern and a full reporting of the genetic diversity estimates associated with the evaluated clusters.