Find research datasets worth reusing
Search datasets from major research repositories and use ShareScore to quickly assess how well each record supports discovery, access, and reuse.
26
datasets available to search
ShareScore release 0.9.0
Dataset results
26 results for “Great Lakes Region”
Upper Midwest Great Lakes Region Citizen Secchi Data 1938 - 2012
Upper MidwestorGreat Lakes Region Citiizen Secchi Data includes 239,741 citizen Secchi monitoring records (1938 – 2012) from Illinois Volunteer Lake Monitoring Program, Indiana Clean Lakes Program, Iowa Secchi Dip-In Project, Michigan Clean Water Corps, Lakes of Missouri Volunteer Program, Minnesota Citizen Lake Monitoring Program, Ohio Citizen Lake Awareness Program, and Wisconsin Citizen Lake Monitoring Records. Data were obtained from above monitoring groups and merged with the high resolution National Hydrography Dataset (www.nhd.usgs.gov) based on citizen proved latitudeorlongitude coordinates to verify the location of individual lakes and size of lake (hectare). Code used to estimate annual average Secchi depth (m) provided in metadata. These citizen-collected, publically available Secchi depth measurements were collected to answer two questions: (1) what are the long-term trends in lake water quality across a broad geographic region?; (2) how do trends differ as a function of spatial location, size of lake monitored, and when Secchi records were collected. Data collection and analysis were funded by the National Science Foundation (MSB- 1065786, EF-1065818, EF-1065649), NTL-LTER (DEB-0822700), STRIVE grant 2011-W-FS-7 from the Environmental Protection Agency. GLERL contribution number (1703).
Population-adjusted pseudo global warming simulations over the Great Lakes Region
<p>Summaries of pseudo global warming simulations over the Great Lakes Region. Specifics below:</p> <p> </p> <p>Each CSV file provides regional summaries from PGW simulations, either over land, for urban grids, or rural grids. This includes cumulative hours above critical heat stress threholds as well as their population-adjusted values.</p> <p>The 'Future_sensitivities_land.csv' file calculates heat stress in the future by keeping all variables except one the same value as the historical run.</p> <p>Among the geotiffs, _perc_land files include percentage of hours in summer above the National Weather Service heat index and wet bulb globe temperature thresholds, _pop_land incorporate population adjusted heat stress above those thresholds, the TEMP_contribution files estimate changes in heat stress if only air temperature changed and all variables remained the same as historical values and the HI_ and WBGT_pop rasters include summer average heat stress and their corresponding populations. </p> <p>See Chakraborty et al. Under Review (will be updated on paper publication) for more details.</p>
Fig. 3 in Field sampling methods for Asiatic garden beetle (Coleoptera: Scarabaeidae) adult movement and flight in the Great Lakes region
Fig. 3. Mean number of Maladera formosae adults captured in milkjug traps containing either water, ethylene glycol antifreeze, or propylene glycol antifreeze, from 14 to 21 Jul 2021 (a) and from 21 to 28 Jul 2021 (b) in soybean at the Fulton3 site near Wauseon, Ohio. Uppercase letter(s) above each bar indicates significant differences at the P ≤ 0.05 level from pairwise comparison analyses.
Fig. 2 in Field sampling methods for Asiatic garden beetle (Coleoptera: Scarabaeidae) adult movement and flight in the Great Lakes region
Fig. 2. Mean number of Maladera formosae adults captured in pitfall traps during individual evaluation periods at Fulton1 (a) and Fulton2 (b) sites, in northwest Ohio. Uppercase letter(s) above each bar indicates significant differences at the P ≤ 0.05 level from pairwise comparison analyses. Traps were deployed on 28 Jun 2017, 1 wk prior to the sampling data indicated in each figure.
Fig. 1 in Field sampling methods for Asiatic garden beetle (Coleoptera: Scarabaeidae) adult movement and flight in the Great Lakes region
Fig. 1. Sampling methods for Maladera formosae adults: within field – pitfall trap (a) and yellow sticky card (b); at field edge – blacklight trap (c), and antifreeze milkjug trap (d). Photo credit: Adrian Pekarcik, The Ohio State University, Wooster, Ohio, USA.
Data from: Optimization of wetland environmental DNA metabarcoding protocols for Great Lakes region herpetofauna
Open the record for dataset details and reuse information.
Data from: Climate connectivity of the bobcat in the Great Lakes region
<p>The Great Lakes and the St. Lawrence River are imposing barriers for wildlife and the additive effect of urban and agricultural development that dominates the lower Great Lakes region likely further reduces functional connectivity for many terrestrial species. As the climate warms species will need to track climate across these barriers. It is important, therefore, to investigate land cover and bioclimatic hypotheses that may explain the northward expansion of species through the Great Lakes. We investigated the functional connectivity of a vagile generalist, the bobcat, as a representative generalist forest species common to the region. We genotyped tissue samples collected across the region at 14 microsatellite loci and compared different landscape hypotheses that might explain the observed gene flow or functional connectivity. We found that the Great Lakes and the additive influence of forest stands with either low or high canopy cover and deep lake-effect snow have disrupted gene flow, whereas intermediate forest cover has facilitated gene flow. Functional connectivity in southern Ontario is relatively low and was limited in part by the low amount of forest cover. Pathways across the Great Lakes were through the Niagara region and through the Lower Peninsula of Michigan over the Straits of Mackinac and the St. Mary's River. These pathways are important routes for bobcat range expansion north of the Great Lakes and are also likely pathways that many other mobile habitat generalists must navigate to track the changing climate. The extent to which species can navigate these routes will be important for determining the future biodiversity of areas north of the Great Lakes.</p>
Data from: Comparative productivity of six bioenergy cropping systems on marginal lands in the Great Lakes Region, United States
<p>Growing lignocellulosic crops on marginal lands is a promising solution for sustainable biofuel production. We evaluated the productivity of bioenergy cropping systems (switchgrass [<em>Panicum</em> <em>virgatum</em> L., var. Cave‐In‐Rock], miscanthus [<em>Miscanthus</em> × <em>giganteus</em>, 'Illinois clone'], hybrid poplar [<em>Populus</em> <em>nigra</em> × <em>P. maximowiczii</em> A. Henry 'NM6'], native grasses [five species], early successional vegetation, and restored prairie vs. historical vegetation [as reference control]) with and without nitrogen fertilization on low‐fertility former cropland at five sites in the Great Lakes Region, United States. We reported biomass yields for the first 7 years after establishment. Switchgrass was most consistently productive across all sites, but miscanthus was more productive at three of the five sites. When averaged across sites, years, and nitrogen (N) treatments, biomass yields followed the order miscanthus > switchgrass > hybrid poplar ≈ native grasses > restored prairie > early successional vegetation ≈ historical vegetation, but varied substantially by crop and site, with a significant crop by site interaction. Yields of miscanthus and switchgrass peaked after four to five growing seasons and declined thereafter, while yields of both native grasses and restored prairie increased throughout 6 years with no sign of follow‐on decline, suggesting that polycultures may outperform monocultures over the long term. Yields of early successional vegetation—similar in composition to historical vegetation at each site—did not improve with time. Nitrogen fertilization increased the yields of all cropping systems at all sites. Our results demonstrate the viability of low‐productivity former cropland for long‐term bioenergy production and suggest there is no single crop best suited for all low-fertility soils.</p>
Phylogeography and genetic variation in Western Jacob's ladder (Polemonium occidentale) provide insights into the origin and conservation of rare species in the Great Lakes region
<p>The perennial herb Western Jacob's Ladder (<em>Polemonium</em> <em>occidentale</em>, Polemoniaceae) is widespread in the mountains of western North America but reappears as a disjunct in the Great Lakes Region in Minnesota and Wisconsin, USA as the narrow endemic<em> P. occidentale </em>subsp. <em>lacustre</em>. This distribution is shown by a diverse assemblage of angiosperms. It has been hypothesized that these species became isolated just after the Last Glacial Maximum, but this has not been tested. Additionally, the genetic diversity and population connectivity of the endemic Great Lakes flora has been understudied, with important conservation implications. Using Genotyping-by-sequencing, we examined the relationship of <em>P</em>. <em>occidentale</em> subsp. <em>lacustre</em> to its closest relatives, relationships among all known populations, and genetic diversity within these populations. <em>Polemonium</em> <em>occidentale</em> subsp. <em>lacustre</em> represents an isolated, unique lineage that diverged from its closest relatives 1.3 ma and arrived in the Great Lakes Region by at least 38 ka. Nearly all extant populations diverged prior to the Last Glacial Maximum, are largely genetically distinct, and show relatively little within-population genetic diversity. Clonality may mitigate reduction in diversity due to drift. Mixed population signal between Wisconsin and some Minnesota populations may be due to gene flow during the Late Pleistocene. While populations of <em>Polemonium</em> <em>occidentale</em> subsp. <em>lacustre</em> may be relictual from a now-extinct western relative, it is best treated as a distinct species. Conservation efforts should focus more on ensuring that current populations remain rather than maintaining large population sizes across a few populations. However, encouraging habitat heterogeneity may accomplish both simultaneously.</p>
Gray wolf range in the western Great Lakes region under forecasted land use and climate change
<p>Land use and climate alter species distributions worldwide, and detecting and understanding how species ranges shift can facilitate conservation planning and action. Following extirpation from most of the contiguous USA, gray wolves (<em>Canis</em> <em>lupus</em>) have partially recolonized former range in the western Great Lakes region, but it is unknown how land use and climate change may alter amounts of wolf habitat. Using wolf observation data collected during winters 2017–2020 in Minnesota, Wisconsin, and Michigan, we created ensemble models to predict how land use and climate change may affect the amount of wolf habitat within these states. A projection model for the western Great Lakes region suggested three of four scenarios of land use and climate change will lead to 9–35% increases in wolf habitat, while a solely climate-based projection model supported our expectation that changes in climate, in isolation, will have limited effect on current wolf range. Our results support stable or increasing amounts of wolf habitat in the western Great Lakes region during the 21st century, suggesting limited or no adverse effects on the current distribution or further recolonization of wolves. Our findings can inform policy development regarding wolf conservation, and identify areas where recolonization is plausible, thus where promoting human-wolf co-existence is most pertinent.</p>
Data from: Comparative productivity of six bioenergy cropping systems on marginal lands in the Great Lakes Region, United States
Open the record for dataset details and reuse information.
Gray wolf range in the western Great Lakes region under forecasted land use and climate change
Open the record for dataset details and reuse information.
Phylogeography and genetic variation in Western Jacob's ladder (Polemonium occidentale) provide insights into the origin and conservation of rare species in the Great Lakes region
Open the record for dataset details and reuse information.
Data from: Climate connectivity of the bobcat in the Great Lakes region
Open the record for dataset details and reuse information.
Subspecies and Distribution. T. t. taxus Schreber, 1778 — S Canada (Alberta, British Columbia, Manitoba, Ontario & Saskatschewan) and NC USA. T. t. berlandieri Baird, 1858 — N & C Mexico and SC USA (W of the Mississippi River). T. t. jacksoni Schantz, 1946 — NE USA (Great Lakes Region). T. t. jeffersonii Harlan, 1825 — W USA (NW to California). in Mustelidae
Subspecies and Distribution. T. t. taxus Schreber, 1778 — S Canada (Alberta, British Columbia, Manitoba, Ontario & Saskatschewan) and NC USA. T. t. berlandieri Baird, 1858 — N & C Mexico and SC USA (W of the Mississippi River). T. t. jacksoni Schantz, 1946 — NE USA (Great Lakes Region). T. t. jeffersonii Harlan, 1825 — W USA (NW to California).
Subspecies and Distribution. S. s. scrofa Linnaeus, 1758 — W Europe, from Denmark, Germany, Poland, and Czech Republic to N Italy and N Iberian Peninsula; possibly also Albania. The taxonomic status of animals in Austria, Switzerland, Slovenia, and Slovakia is unclear but presumably these populations are included in scrofa, as are the populations of Sweden, Finland, and the Baltic states. However, restocking of once depleted populations, for example in Italy, has likely involved the introduction and mixing of this subspecies with other subspecies, such as attila. S. s. affinis Gray, 1847 — S India and Sri Lanka. S. s. algirus Loche, 1867 — Tunisia, Algeria, and Morocco, on the coastal side of the mountains or in the low montane areas. S. s. attila Thomas, 1912 — Hungary, Ukraine, C & S Belarus, Romania, Moldova, and S Russia towards the N flank of the Caucasus, but not including the Transcaucasian countries of Georgia, Armenia, and Azerbaijan. The range possibly extends as far S as the Mesopotamian Delta in Iraq, in which case it would likely include W & SW Iran, and possibly E Turkey and Syria, where it borders with lybicus. Such a range could not be easily reconciled with a statement by Groves that "the difference between pigs from N and S of the Caucasus is quite striking; Transcaucasian boars are certainly not attila." This subspecies may also extend into C Asia and include Kazakhstan, Uzbekistan, and Turkmenistan, but no data exist to support this. S. s. baeticus Thomas, 1912 — originally described from Coto Donana, S Spain, and later merged with meridionalis; also S Portugal. Unless evidence is found that these Italian and Iberian populations are the relics of a much larger formerly contiguous range, this subspecies should be kept as distinct. S. s. coreanus Heude, 1897 — Korean Peninsula. S. s. eristatus Wagner, 1839 — Himalayas S to C India and E to Indochina (N of the Kra Isthmus). S. s. davidi Groves, 1981 — the arid zone from E Iran to Gujarat, including Pakistan and NW India, and perhaps N to Tajikistan. S. s. leucomystax Temminck, 1842 — main Is ofJapan (Honshu, Shikoku, Kyushu, Nakadori, Hiburijima, Tojima, Kushima, and other smaller Is). S. s. lybicus Gray, 1868 — Bulgaria, Greece, Turkey, Syria, Jordan, Israel, Palestine, in the past also in Lybia, and Egypt. The former Yugoslavia was included in its range, which would suggest that now Slovenia, Serbia, Croatia, Bosnia and Herzegovina, Montenegro, and Kosovo are within the range of this subspecies, although the exact boundaries are unclear. Pigs from Albania have been assigned to S. s. scrofa. S. s. majori De Beaux & Festa, 1927 — C & S Italian Peninsula. S. s. menidionalis Forsyth Major, 1882 — Corsica and Sardinia, with the proviso that the two populations are very likely to be introduced or feral. S. s. moupinensis Milne-Edwards, 1871 — China, S to Vietnam and W to Sichuan. S. s. nigripes Blanford, 1875 — the flanks of the Tianshan mountains in Kyrgyzstan and NW China (Xinjiang). An animal photographed in NE Iran (Golestan) looked like this subspecies. S. s. nukiuanus Kuroda, 1924 — Iriomote, Ishigaki, Okinawa, Tokunoshima, Amamioshima, and Kakerome Is in the Ryukyu chain in extreme S Japan, though some of these populations have hybridized with introduced domesticates. S. s. sibiricus Staffe, 1922 — Mongolia and Transbaikal (S & E of Lake Baikal). S. s. tawvanus Swinhoe, 1863 — Taiwan. S. s. ussuricus Heude, 1888 — far E Russia and the Manchurian region (China). Korean populations were previously included in this subspecies, but based on new evidence, the Korean taxon seems more similar to moupinensis. S. s. vittatus Boie, 1828 — Malay Peninsula, S of the Isthmus of Kra, the offshore islands of Terutai and Langkawi, Sumatra, Riau Archipelago, Java, Bali, and a range of smaller islands around these, including Babi, Bakong, Batam, Bawean, Bengkalis, Bintan, Bulan, Bunguran, Cuyo, Deli, Durian, Enggano, Galang, Jambongan, Karimon (Riau Is), Kundur, Lagong, Laut, Lingga, Lingung, Mapor, Moro Kecil, North Pagai, Nias, Panaitan, Payong, Penang, Pinie, Rupat, Siantan, Siberut, Simeulue, Singkep, Sugi, Sugi Bawa, Telibon, Tinggi, Tuangku, and the Tambelan Is. This species was originally present from the British Is in the extreme W, through Eurasia from S Scandinavia to S Siberia, extending as far E as Korea and Japan, and SE into some of the Sunda Is and Taiwan. In the S the species ranged along the Nile Valley to Khartoum, and N of the Sahara in Africa, more orless following the continental coasts of S, E, and SE Asia. Within this range it was absent only from extremely dry deserts, e.g. the driest regions of Mongolia and in China W of Sichuan; and alpine zones, such as the high altitudes of Pamir and Tien Shan. In recent centuries, the range of S. scrofa has changed dramatically because of hunting and changes in available habitat. The species disappeared from the British Is in the 17" century, from Denmark in the 19" century, and was greatly reduced in range and numbers in the 20" century from areas as distant as Tunisia, Sudan, Germany, and Russia. Following these severe declines, there were some slight population recoveries in Russia, Italy, Spain, and Germany in the mid-20™ century, and natural and assisted range expansions in Denmark and Sweden. The species has also been inadvertently reintroduced in various locations in the Great Britain via escapees of mixed origin from commercial farming enterprises. Ex-S. scrofa stocks also occur as introduced feral populations in various other parts of the world, including Australia, New Zealand, the eastern Malay Archipelago, and in North, Central, and South America. In all of these areas they are now generally recognized as a major pest. in Suidae
Subspecies and Distribution. S. s. scrofa Linnaeus, 1758 — W Europe, from Denmark, Germany, Poland, and Czech Republic to N Italy and N Iberian Peninsula; possibly also Albania. The taxonomic status of animals in Austria, Switzerland, Slovenia, and Slovakia is unclear but presumably these populations are included in scrofa, as are the populations of Sweden, Finland, and the Baltic states. However, restocking of once depleted populations, for example in Italy, has likely involved the introduction and mixing of this subspecies with other subspecies, such as attila. S. s. affinis Gray, 1847 — S India and Sri Lanka. S. s. algirus Loche, 1867 — Tunisia, Algeria, and Morocco, on the coastal side of the mountains or in the low montane areas. S. s. attila Thomas, 1912 — Hungary, Ukraine, C & S Belarus, Romania, Moldova, and S Russia towards the N flank of the Caucasus, but not including the Transcaucasian countries of Georgia, Armenia, and Azerbaijan. The range possibly extends as far S as the Mesopotamian Delta in Iraq, in which case it would likely include W & SW Iran, and possibly E Turkey and Syria, where it borders with lybicus. Such a range could not be easily reconciled with a statement by Groves that "the difference between pigs from N and S of the Caucasus is quite striking; Transcaucasian boars are certainly not attila." This subspecies may also extend into C Asia and include Kazakhstan, Uzbekistan, and Turkmenistan, but no data exist to support this. S. s. baeticus Thomas, 1912 — originally described from Coto Donana, S Spain, and later merged with meridionalis; also S Portugal. Unless evidence is found that these Italian and Iberian populations are the relics of a much larger formerly contiguous range, this subspecies should be kept as distinct. S. s. coreanus Heude, 1897 — Korean Peninsula. S. s. eristatus Wagner, 1839 — Himalayas S to C India and E to Indochina (N of the Kra Isthmus). S. s. davidi Groves, 1981 — the arid zone from E Iran to Gujarat, including Pakistan and NW India, and perhaps N to Tajikistan. S. s. leucomystax Temminck, 1842 — main Is ofJapan (Honshu, Shikoku, Kyushu, Nakadori, Hiburijima, Tojima, Kushima, and other smaller Is). S. s. lybicus Gray, 1868 — Bulgaria, Greece, Turkey, Syria, Jordan, Israel, Palestine, in the past also in Lybia, and Egypt. The former Yugoslavia was included in its range, which would suggest that now Slovenia, Serbia, Croatia, Bosnia and Herzegovina, Montenegro, and Kosovo are within the range of this subspecies, although the exact boundaries are unclear. Pigs from Albania have been assigned to S. s. scrofa. S. s. majori De Beaux & Festa, 1927 — C & S Italian Peninsula. S. s. menidionalis Forsyth Major, 1882 — Corsica and Sardinia, with the proviso that the two populations are very likely to be introduced or feral. S. s. moupinensis Milne-Edwards, 1871 — China, S to Vietnam and W to Sichuan. S. s. nigripes Blanford, 1875 — the flanks of the Tianshan mountains in Kyrgyzstan and NW China (Xinjiang). An animal photographed in NE Iran (Golestan) looked like this subspecies. S. s. nukiuanus Kuroda, 1924 — Iriomote, Ishigaki, Okinawa, Tokunoshima, Amamioshima, and Kakerome Is in the Ryukyu chain in extreme S Japan, though some of these populations have hybridized with introduced domesticates. S. s. sibiricus Staffe, 1922 — Mongolia and Transbaikal (S & E of Lake Baikal). S. s. tawvanus Swinhoe, 1863 — Taiwan. S. s. ussuricus Heude, 1888 — far E Russia and the Manchurian region (China). Korean populations were previously included in this subspecies, but based on new evidence, the Korean taxon seems more similar to moupinensis. S. s. vittatus Boie, 1828 — Malay Peninsula, S of the Isthmus of Kra, the offshore islands of Terutai and Langkawi, Sumatra, Riau Archipelago, Java, Bali, and a range of smaller islands around these, including Babi, Bakong, Batam, Bawean, Bengkalis, Bintan, Bulan, Bunguran, Cuyo, Deli, Durian, Enggano, Galang, Jambongan, Karimon (Riau Is), Kundur, Lagong, Laut, Lingga, Lingung, Mapor, Moro Kecil, North Pagai, Nias, Panaitan, Payong, Penang, Pinie, Rupat, Siantan, Siberut, Simeulue, Singkep, Sugi, Sugi Bawa, Telibon, Tinggi, Tuangku, and the Tambelan Is. This species was originally present from the British Is in the extreme W, through Eurasia from S Scandinavia to S Siberia, extending as far E as Korea and Japan, and SE into some of the Sunda Is and Taiwan. In the S the species ranged along the Nile Valley to Khartoum, and N of the Sahara in Africa, more orless following the continental coasts of S, E, and SE Asia. Within this range it was absent only from extremely dry deserts, e.g. the driest regions of Mongolia and in China W of Sichuan; and alpine zones, such as the high altitudes of Pamir and Tien Shan. In recent centuries, the range of S. scrofa has changed dramatically because of hunting and changes in available habitat. The species disappeared from the British Is in the 17" century, from Denmark in the 19" century, and was greatly reduced in range and numbers in the 20" century from areas as distant as Tunisia, Sudan, Germany, and Russia. Following these severe declines, there were some slight population recoveries in Russia, Italy, Spain, and Germany in the mid-20™ century, and natural and assisted range expansions in Denmark and Sweden. The species has also been inadvertently reintroduced in various locations in the Great Britain via escapees of mixed origin from commercial farming enterprises. Ex-S. scrofa stocks also occur as introduced feral populations in various other parts of the world, including Australia, New Zealand, the eastern Malay Archipelago, and in North, Central, and South America. In all of these areas they are now generally recognized as a major pest.
Validation Data used for manuscript "Climate Projections over the Great Lakes Region: Using Two-way Coupling of a Regional Climate Model with a 3-D Lake Model"
<p>those are the processed data that used for model-data comparison in the manuscript "Climate Projections over the Great Lakes Region: Using Two-way Coupling of a Regional Climate Model with a 3-D Lake Model", including Lake Surface Temperature and Lake Surface Ice Cover from Great Lakes Surface Environmental Analysis (GLSEA), Surface Air temperature and Precipitation from Climatic Research Unit (CRU). </p>
Subspecies and Distribution. P.m.maniculatusWagner,1845—SManitoba,Ontario,Quebec,andLabrador,Canada. P.m.abietorumBangs,1896—NewBrunswickandNovaScotia,Canada,andMaine, USA. P.m.alpinusCowan,1937—restrictedtoasmallregioninSEBritishColumbia,Canada . P.m.anacapaevonBloeker,1942—knownonlyfromWestAnacapaIandsurroundingIs,California,USA. P.m.angustusHall,1932—knownonlyfromSWpartofVancouverI,BritishColumbia, Canada. P.m.anticostiensisMoulthrop,1937—knownonlyfromthetypelocalityonEAnticostiI,Quebec,Canada. P.m.argentatusCopeland&Church,1906—knownonlyfromthetypelocalityonGrandMananI,NewBrunswick,Canada. P.m.artemisiaeRhoads,1894—fromSCBritishColumbia,Canada,SWtoWWyoming, USA. P.m.assimilisNelson&Goldman,1931—knownonlyfromthetypelocalityonCoronadoIs,BajaCalifornia,Mexico. P.m.austerusBaird,1855—WCWashington,USA. P.m.bairdiiHoy&Kennicott,1857—mostoftheECportionoftheUSA. P.m.balaclavaeMcCabe&Cowan,1945—knownonlyfromthetypelocalityonBalaklavaI,BritishColumbia,Canada. P.m.blandusOsgood,1904—SCUSAStoSanLuisPotosi,Guanajauto,andJalisco, Mexico. P.m.borealisMearns,1911—NWCanada. P.m.catalinaeElliot,1903—knownonlyfromSantaCatalinaI,California,USA. P.m.cmenitius|.A.Allen,1898—knownonlyfromthetypelocalityonSanRoqueI, BajaCalifornia,Mexico. P.m.clementisMearns,1896—knownonlyfromSanClementeI,California,USA. P.m.coolidge:Thomas,1898—SBajaCaliforniaandBajaCaliforniaSur,Mexico. P.m.dorsalisNelson&Goldman,1931—knownonlyfromthetypelocalityonNatividadI,BajaCalifornia,Mexico. P.m.dubiusJ.A.Allen,1898—knownonlyfromthetypelocalityonTodosSantosI, BajaCalifornia,Mexico. P.m.elususNelson&Goldman,1931—knownonlyfromSantaBarabaraandSutilIs, California,USA. P.m.eremusOsgood,1909—knownonlyfromGrindstoneI,Quebec,Canada. P.m.exiguusJ.A.Allen,1898—knownonlyfromSanMartinI,BajaCalifornia,Mexico. P.m.exterusNelson&Goldman,1931—knownonlyfromthetypelocalityonSanNicolasI,California,USA. P.m.fulvusOsgood,1904—fromCPueblaandVeracruzStoCOaxaca,Mexico. P.m.gambeliiBaird,1858—N&WCalifornia,USA,SintoNBajaCalifornia,Mexico. P.m.georgiensisHall,1938—knownonlyfromthetypelocalityonTexadaIandsurroundingIs,BritishColumbia,Canada. P.m.geronimensisJ.A.Allen,1898—knownonlyfromthetypelocalityonSanGeronimoI,BajaCalifornia,Mexico. P.m.gracilisLeConte,1855—OntarioandSQuebec,Canada,S&EtoWisconsin, Michigan,andNEUSA.FP.m.hollister:Osgood,1909—knownonlyfromSanJuanIandsurroundingIs,Washington,USA. P.m.huey:Nelson&Goldman,1932—knownonlyfromthetypelocalityonasmallunnamedIinGonzagaBay,BajaCalifornia,Mexico. P. m. inclarus Goldman, 1939 — known only from Fremont I in Great Salt Lake, Utah, USA. P.m. labecula Elliot, 1903 — from Durango S to Michoacan and Morelos, Mexico. P. m. luteus Osgood, 1905 — from South Dakota S to W Texas, USA. P. m. magdalenae Osgood, 1909 — Magdalena I and surrounding mainland areas, Baja California, Mexico. P.m. margaritae Osgood, 1909 — known only from Margarita I, Baja California, Mexico. Pm. nebrascensis Coues, 1877 — from S Alberta and Saskatchewan, Canada, S to NW Texas, USA. Pm. nubiterrae Rhoads, 1896 — from W New York S to North Carolina, USA. Pm. ozarkiarum Black, 1935 — from NE Oklahoma and SW Missouri S to W Arkansas and NC edge of Texas, USA. P. m. pallescensJ. A. Allen, 1896 — NC to SC Texas, USA. Pm. plumbeus C. F. Jackson, 1939 — E Quebec, Canada. Pm. rubidus Osgood, 1901 — from SW Washington S along the Pacific Coast to C California, USA. P. m. rufinus Merriam, 1890 — from N California S to SC Arizona and New Mexico, USA. P. m. sanctaerosae von Bloeker, 1940 — known only from Santa Rosa I, California, USA. P.m. santacruzae Nelson & Goldman, 1931 — known only from Santa Cruz I, California, USA. Pm. saturatus Bangs, 1897 — known only from Saturna I, British Columbia, Canada. Pm. saxamans McCabe & Cowan, 1945 — known only from Duncan I and surrounding Is, British Columbia, Canada. Pm. serratus Davis, 1939 — restricted to a small region in C Idaho, USA. Pm. sonoriensis Le Conte, 1853 — from SE Oregon and S Idaho, USA, S to N edge of Sonora, Mexico. Pm. streatori Nelson & Goldman, 1931 — known only from San Miguel I and surrounding Is, California, USA. in Cricetidae
Subspecies and Distribution. P.m.maniculatusWagner,1845—SManitoba,Ontario,Quebec,andLabrador,Canada. P.m.abietorumBangs,1896—NewBrunswickandNovaScotia,Canada,andMaine, USA. P.m.alpinusCowan,1937—restrictedtoasmallregioninSEBritishColumbia,Canada . P.m.anacapaevonBloeker,1942—knownonlyfromWestAnacapaIandsurroundingIs,California,USA. P.m.angustusHall,1932—knownonlyfromSWpartofVancouverI,BritishColumbia, Canada. P.m.anticostiensisMoulthrop,1937—knownonlyfromthetypelocalityonEAnticostiI,Quebec,Canada. P.m.argentatusCopeland&Church,1906—knownonlyfromthetypelocalityonGrandMananI,NewBrunswick,Canada. P.m.artemisiaeRhoads,1894—fromSCBritishColumbia,Canada,SWtoWWyoming, USA. P.m.assimilisNelson&Goldman,1931—knownonlyfromthetypelocalityonCoronadoIs,BajaCalifornia,Mexico. P.m.austerusBaird,1855—WCWashington,USA. P.m.bairdiiHoy&Kennicott,1857—mostoftheECportionoftheUSA. P.m.balaclavaeMcCabe&Cowan,1945—knownonlyfromthetypelocalityonBalaklavaI,BritishColumbia,Canada. P.m.blandusOsgood,1904—SCUSAStoSanLuisPotosi,Guanajauto,andJalisco, Mexico. P.m.borealisMearns,1911—NWCanada. P.m.catalinaeElliot,1903—knownonlyfromSantaCatalinaI,California,USA. P.m.cmenitius|.A.Allen,1898—knownonlyfromthetypelocalityonSanRoqueI, BajaCalifornia,Mexico. P.m.clementisMearns,1896—knownonlyfromSanClementeI,California,USA. P.m.coolidge:Thomas,1898—SBajaCaliforniaandBajaCaliforniaSur,Mexico. P.m.dorsalisNelson&Goldman,1931—knownonlyfromthetypelocalityonNatividadI,BajaCalifornia,Mexico. P.m.dubiusJ.A.Allen,1898—knownonlyfromthetypelocalityonTodosSantosI, BajaCalifornia,Mexico. P.m.elususNelson&Goldman,1931—knownonlyfromSantaBarabaraandSutilIs, California,USA. P.m.eremusOsgood,1909—knownonlyfromGrindstoneI,Quebec,Canada. P.m.exiguusJ.A.Allen,1898—knownonlyfromSanMartinI,BajaCalifornia,Mexico. P.m.exterusNelson&Goldman,1931—knownonlyfromthetypelocalityonSanNicolasI,California,USA. P.m.fulvusOsgood,1904—fromCPueblaandVeracruzStoCOaxaca,Mexico. P.m.gambeliiBaird,1858—N&WCalifornia,USA,SintoNBajaCalifornia,Mexico. P.m.georgiensisHall,1938—knownonlyfromthetypelocalityonTexadaIandsurroundingIs,BritishColumbia,Canada. P.m.geronimensisJ.A.Allen,1898—knownonlyfromthetypelocalityonSanGeronimoI,BajaCalifornia,Mexico. P.m.gracilisLeConte,1855—OntarioandSQuebec,Canada,S&EtoWisconsin, Michigan,andNEUSA.FP.m.hollister:Osgood,1909—knownonlyfromSanJuanIandsurroundingIs,Washington,USA. P.m.huey:Nelson&Goldman,1932—knownonlyfromthetypelocalityonasmallunnamedIinGonzagaBay,BajaCalifornia,Mexico. P. m. inclarus Goldman, 1939 — known only from Fremont I in Great Salt Lake, Utah, USA. P.m. labecula Elliot, 1903 — from Durango S to Michoacan and Morelos, Mexico. P. m. luteus Osgood, 1905 — from South Dakota S to W Texas, USA. P. m. magdalenae Osgood, 1909 — Magdalena I and surrounding mainland areas, Baja California, Mexico. P.m. margaritae Osgood, 1909 — known only from Margarita I, Baja California, Mexico. Pm. nebrascensis Coues, 1877 — from S Alberta and Saskatchewan, Canada, S to NW Texas, USA. Pm. nubiterrae Rhoads, 1896 — from W New York S to North Carolina, USA. Pm. ozarkiarum Black, 1935 — from NE Oklahoma and SW Missouri S to W Arkansas and NC edge of Texas, USA. P. m. pallescensJ. A. Allen, 1896 — NC to SC Texas, USA. Pm. plumbeus C. F. Jackson, 1939 — E Quebec, Canada. Pm. rubidus Osgood, 1901 — from SW Washington S along the Pacific Coast to C California, USA. P. m. rufinus Merriam, 1890 — from N California S to SC Arizona and New Mexico, USA. P. m. sanctaerosae von Bloeker, 1940 — known only from Santa Rosa I, California, USA. P.m. santacruzae Nelson & Goldman, 1931 — known only from Santa Cruz I, California, USA. Pm. saturatus Bangs, 1897 — known only from Saturna I, British Columbia, Canada. Pm. saxamans McCabe & Cowan, 1945 — known only from Duncan I and surrounding Is, British Columbia, Canada. Pm. serratus Davis, 1939 — restricted to a small region in C Idaho, USA. Pm. sonoriensis Le Conte, 1853 — from SE Oregon and S Idaho, USA, S to N edge of Sonora, Mexico. Pm. streatori Nelson & Goldman, 1931 — known only from San Miguel I and surrounding Is, California, USA.
Sensitivity of multiple vital rates for ruffed grouse in the upper Great Lakes region
<p>Effective management of wildlife requires a full understanding of population dynamics and knowledge of potential drivers that influence population growth. The Ruffed Grouse (<i>Bonasa umbellus</i>) is a popular upland game bird widely distributed across the northern United States and Canada that has experienced population declines within portions of its range in response to forest maturation and habitat loss. Although the species has been extensively studied, few efforts have been made to synthesize demographic data into a sensitivity analysis to guide management actions. We reviewed the literature and compiled Ruffed Grouse vital rates from 14 field studies conducted across four decades (1982−2018) within the Upper Great Lakes region of Michigan, Minnesota, and Wisconsin, USA. We parameterized a deterministic matrix model to evaluate population dynamics and conducted sensitivity analyses to identify vital rates projected to have the greatest influence on the finite rate of population change (λ). Our modeling effort projected a stable but highly variable annual rate of population change (λ = 1.01; 95% CI = 0.88–1.14) for Ruffed Grouse in the Upper Great Lakes region. Stochastic rates of population change derived from spring drumming surveys (λ = 1.01; 95% CI = 0.61–1.45) and Christmas Bird Count surveys (λ = 0.99; 95% CI = 0.62–1.76) of the corresponding regional population provided validation of stable trends over the same time period as our demographic model. Prospective elasticities and variance-scaled sensitivities suggested λ would be greatly influenced by components of reproductive performance: nesting success, chick survival, and post-fledging juvenile survival. Retrospective analysis indicated that much of the overall variability in λ and annual productivity was also attributed to annual variation in nesting success. Management of this species has often focused on fall and overwinter survival, but population projection models provided little evidence that survival was the predominant factor affecting population growth of Ruffed Grouse in this region. A suite of confounding factors and demographic processes that drive population trends can differ significantly across a species' range. In the Upper Great Lakes region, management efforts aimed at maximizing reproductive success would likely have the greatest potential influence on Ruffed Grouse population growth. Other types of systematic, regional survey data can also be useful for validating population trends derived from demographic modeling studies.</p>
Supplementary material 1 from: Craves JA, Anich NM (2023) Status and distribution of an introduced population of European Goldfinches (Carduelis carduelis) in the western Great Lakes region of North America. NeoBiota 81: 129-155. https://doi.org/10.3897/neobiota.81.97736
Records of European Goldfinches in North America, 2001–2021, by state/province with county totals. Records represent observations, not individual birds. Regions included in the western Great Lakes region are in bold
ScienceDex guides
Understand access before you commit
These curated guides explain access requirements, typical timelines, costs, and reuse considerations for widely used research datasets.
Allen Brain Atlas
Allen Brain Atlas is an Allen Institute collection of brain map atlases, datasets, APIs, and analysis tools covering mouse, human, and non-human primate brain resources.
Annotated Behaviour and Observability Dataset (ABODe)
ABODe is a University of Edinburgh DataShare dataset for behavior classification in group-housed mice using home-cage video, identities, bounding boxes, ground-plate positions, and annotator labels.
DANDI Archive for NWB datasets
DANDI is a BRAIN Initiative archive for publishing and sharing neurophysiology data, including electrophysiology, optophysiology, and behavioral data packaged as NWB and related standards.
International Brain Laboratory public data
The International Brain Laboratory public data releases expose standardized mouse decision-making experiments, including Neuropixels recordings, widefield calcium imaging, behavior, and session metadata accessed through the ONE API.
OpenNeuro
OpenNeuro is a free, open platform for sharing neuroimaging datasets, with public search, dataset pages, and download paths for web, S3, DataLad, and the OpenNeuro CLI.