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.
53
datasets available to search
ShareScore release 0.9.0
Dataset results
53 results for “small lakes”
Zooplankton of Small Lakes and Wetland Ponds in Wisconsin - North Temperate Lakes LTER 1996
We sampled zooplankton communities from 54 small water bodies distributed throughout Wisconsin to evaluate whether a snap-shot of zooplankton community structure during early spring could be used for the purpose of differentiating lakes from wetlands. We collected a single set of zooplankton and water chemistry data during a one-month time window (synchronized from south to north across the state) from an open water site in each basin as a means to minimize and standardize sampling effort and to minimize cascading effects arising from predator-prey interactions with resident and immigrant aquatic insect communities. We identified 53 taxa of zooplankton from 54 sites sampled across Wisconsin. There was an average of 6.83 taxa per site. The zooplankton species were distributed with a great deal of independence. We did not detect significant correlations between number of taxa and geographic region or waterbody size. There was a significant inverse correlation between number of taxa and the concentration of calcium ion, alkalinity and conductivity. One pair of taxa, Lynceus brachyurus and Chaoborus americanus, showed a significant difference in average duration of sites of their respective occurrence. All other pairs of taxa had no significant difference in average latitude, waterbody surface area, total phosphorus, total Kjeldahl nitrogen, alkalinity, conductivity, calcium ion, sulfate, nitrate, silicate or chloride. Taxa were distributed at random among the sites - there were no statistically significant pairs of taxa occurring together or avoiding each other. Multivariate analysis of zooplankton associations showed no evidence of distinct associations that could be used to distinguish lakes from wetlands. Zooplankton community structure appears to be a poor tool for distinguishing between lakes and wetlands, especially at the relatively large scale of Wisconsin (dimension of about 500 km). The data suggest that a small body of water in Wisconsin could be classified
Indicative distribution map for Ecosystem Functional Group F2.2 Small permanent freshwater lakes
<p>This archive contains indicative distribution maps and profiles for <strong>F2.2 Small permanent freshwater lakes</strong>, a ecosystem functional group (EFG, level 3) of the <a href="https://global-ecosystems.org/">IUCN Global Ecosystem Typology</a> (v2.0). Please refer to Keith <em>et al.</em> (2020) for details.</p> <p>The descriptive profiles provide brief summaries of key ecological traits and processes, maps are indicative of global distribution patterns, and are not intended to represent fine-scale patterns. The maps show areas of the world containing major (value of 1, coloured red) or minor occurrences (value of 2, coloured yellow) of each ecosystem functional group. Minor occurrences are areas where an ecosystem functional group is scattered in patches within matrices of other ecosystem functional groups or where they occur in substantial areas, but only within a segment of a larger region. Given bounds of resolution and accuracy of source data, the maps should be used to query which EFG are likely to occur within areas, rather than which occur at particular point locations. Detailed methods and references for the maps are included in the profile (xml format).</p>
Small mammal structure cover collected at Team Vole fences near Nome, Toolik Lake, and Utqaigvik, Alaska, summer 2019
Percent cover of tundra vole and brown lemming structures collected from within the Team Vole enclosure/exclosure fences near Nome, Toolik, Utqiagvik, AK 2019.
Lake morphometry mediates the relationship between water color and fish biomass in small boreal lakes
<p>The data are for an analysis of the influence of water color and lake depth on fish biomass small (1-10 ha) lakes in boreal Sweden.</p> <p>AllBorealLakes.csv contains a list of surface areas (variable name hectares, given in hectares) for all lakes greater or equal to 1 hectare surface area in the boreal zone of Sweden. The original lake census comes from the Swedish government (Nisell et al. 2007) and lakes within the boreal zone were extracted based on the boreal zone boundary of Olson et al. (2001). There is also a lake ID number (FID_vivan_) used in the extraction.</p> <p> </p> <p>SmallBorealLakes.csv contains a list of surface areas (variable name hectares, given in hectares) for all lakes greater or equal to 1 hectare surface area and less than or equal to 10 hectares in the boreal zone of Sweden. The original lake census comes from the Swedish government (Nisell et al. 2007) and lakes within the boreal zone were extracted based on the boreal zone boundary of Olson et al. (2001). There is also a lake ID number (FID_vivan_) used in the extraction.</p> <p> </p> <p>SNILLE_ms_data.csv contains data on fish biomass for 16 small boreal lakes. The geographic coordinates (Northing and Easting) are based on the Swedish Grid, see: http://www.lantmateriet.se. Lake surface areas based on the Swedish lake census (Nisell et al. 2007). Mean depth (meters) is based on echo sounding with an integrated GIS (Lowrance m52i). Volumes were calculated by calculating a triangulated irregular network and then mean depth subsequently calculated as volume divided by surface area. kd is the vertical light extinction coefficient (m^-1). We calculated <em>k</em><sub>d</sub> from the slope of the linear regression of the logarithm of photosynthetically active radiation (measured with LI-COR LI-193 spherical quantum sensor) versus measurement depth (measured in approximately 0.5 meter intervals over the deepest part of the lake). The shallowest measure was excluded from the calculation. The values in the table are the average of kd calculated from three visits to each lake (once each approximately in June, July, and August 2014). kd is an indicator of colored dissolved organic carbon and water color (brownness) in this region and there is relatively little contribution of phytoplankton or inorganic particulate. CPUE Catch-per-unit-effort (kg wet weight / net) is an indicator of fish biomass. For each lake, we set 8 multi mesh gill nets (Nordic 12 nets, 30 x 1.5 m; Mesh sizes: 5, 6.25, 8, 10, 12.5, 15.5, 19.5, 24, 29, 35, 43, 55 mm) over one night (approximately 12 hours) in August 2014. Four nets were deployed in the littoral zone perpendicular to the shoreline. These nets were approximately equally spaced. Two floating nets were deployed across the deepest point of the pelagic zone, and two benthic nets were set in the hypolimnion near the deepest point of the lake. Net-specific catches were averaged with weighting based on the relative extent of the different habitat types (see Karlsson et al. 2015). Specifically, the profundal nets were assumed to represent the total hypolimnetic volume and the pelagic nets were assumed to represent the volume above the hypolimnion. The volume of the littoral nets was calculated by subtracting the volume of the pelagic and profundal habitats from the total lake volume. These weighted CPUE values are given in the file. Species identified through gill netting are abbreviated as: P for European perch (<em>Perca fluviatilis</em>), R for common roach (<em>Rutilus rutilus</em>), N for northern pike (<em>Esox lucius</em>), B for burbot (<em>Lota lota</em>)</p> <p>Boreal_Area_kd_data.csv contains a list of estimated vertical light extinction coefficients (kd, m^-1) for lakes in boreal Sweden. Specifically, the values are based on water chemistry data from a national water quality survey conducted in Sweden every five years. Lake surface water (0.5 m) was sampled from above the deepest part of the lake during early autumn when the water column is mixed. Water quality analyses were performed using standard limnological techniques (detailed methods available on the internet at: http://www.slu.se/en/departments/aquatic-sciences-assessment/laboratories/geochemicallaboratory/water-chemical-analyses/) by a certified water analysis laboratory at the Swedish University of Agricultural Sciences. The data are freely available on the Internet at http://www.slu.se/vatten-miljo. Absorbance at 420 nm (D) which is a metric of water color (brownness) was used to calculate absorption coefficients per meter (a, m-1) from the initial measurement: a = (D * 2.303) / L. where L is the optical path length in meters, 0.05 in the case of the monitoring data. We then estimated kd (m^-1) based on the calibration curve reported by Seekell et al. (2015): = kd = 0.3121 + 0.1327a. These values were associated with surface areas from the Swedish lake census (Nisell et al. 2007) using a identification number common to both the Swedish water chemistry and lake census datasets. Finally, the file was trimmed to only include lakes with surface areas greater or equal to 1 hectare and less than or equal to 10 hectares.</p> <p>References:</p> <ul> <li>Nisell, J., A. Lindsjö, and J. Temnerud (2007), Rikstäckande virtuellt vattendrags nätverk för flödesbaserad modellering VIVAN, [In Swedish], Rapport 2007:17, Institutionen för miljöanalys, SLU.</li> <li>Olson DM, Dinerstein E, Wikramanayake ED, Burgess ND, Powell GVN, Underwood EC, D’amico JA, Itoua I, Strand HE, Morrison JC, Loucks CJ, Allnutt TF, Ricketts TH, Kura Y, Lamoreux JF, Wettengel WW, Hedao P, Kassem KR (2001) Terrestrial ecoregions o the world: A new map of life on Earth. <em>BioScience</em> 51:933-938.</li> <li> <p>Karlsson J, Bergström AK, Byström P, Gudasz C, Rodriguez P, Hein C (2015) Terrestrial organic matter input suppresses biomass production in lake ecosystems. <em>Ecology</em> 96:2870-2876. doi: 10.1890/15-0515.1</p> </li> <li> <p>Seekell DA, Lapierre JF, Karlsson J (2015) Trade-offs between light and nutrient availability across gradients of dissolved organic carbon concentration in Swedish lakes: Implications for patterns in primary production. <em>Canadian Journal of Fisheries and Aquatic Sciences</em> 72:1663-1671. doi: 10.1139/cjfas-2015-0187</p> </li> </ul>
Fig.5 in Genetic And Morphological Variability Of Small Vendace (Coregonus Albula (Linnaeus, 1758)) Population In Three Latvian Lakes
Fig.5. Principal component analysis (PCA) plot of the genetic structuring among the three vendace populations. A). PC1 and PC2 explain 25.50% and 21.88% of the total variation, respectively (by allozyme markers); B). PC1 and PC2 explain 19.52% and 13.73% of the total variation, respectively (by RAPD markers).
Fig. 4 in Genetic And Morphological Variability Of Small Vendace (Coregonus Albula (Linnaeus, 1758)) Population In Three Latvian Lakes
Fig. 4. Number of RAPD loci and gene diversity of Coregonus albula in three Latvian lakes, based on RAPD markers.
Fig.3 in Genetic And Morphological Variability Of Small Vendace (Coregonus Albula (Linnaeus, 1758)) Population In Three Latvian Lakes
Fig.3. Allelic richness and polymorphism in Coregonus albula populations in studied lakes based on allozyme markers.
Text-fig. 2. A – First small excavation trench in the newly discovered fossiliferous outcrop area of the Ploužnice lake horizon, locality "Small Ravine" south of the village Ploužnice on the slope of road No. 286. Typical are the red, violet and varicoloured tuffaceous siltstones. Semily Formation, Late Stephanian, Krkonoše Piedmont Basin. B – Basal part of fossiliferous 12 cm to14 cm thick reddish to purple-red tuffaceous siltstone bed from the trench in Text-fig. 2A. Internal bedding is expressed as horizontal but with diffuse changes in grain size from fine silt to coarse, fine sandy silt. Intercalated in places are 3 to 5 mm thick layers (indicated by arrows) with patchy concentrations of isolated fish remains, especially in the first 3 centimetres of this siltstone layer. The large white spot at 2.5 cm is a coprolite fragment. in Fossil Fauna And Flora Of A Re-Discovered Locality In The Late Carboniferous Ploužnice Horizon Of The Krkonoše Piedmont Basin, Bohemian Massif
Text-fig. 2. A – First small excavation trench in the newly discovered fossiliferous outcrop area of the Ploužnice lake horizon, locality "Small Ravine" south of the village Ploužnice on the slope of road No. 286. Typical are the red, violet and varicoloured tuffaceous siltstones. Semily Formation, Late Stephanian, Krkonoše Piedmont Basin. B – Basal part of fossiliferous 12 cm to14 cm thick reddish to purple-red tuffaceous siltstone bed from the trench in Text-fig. 2A. Internal bedding is expressed as horizontal but with diffuse changes in grain size from fine silt to coarse, fine sandy silt. Intercalated in places are 3 to 5 mm thick layers (indicated by arrows) with patchy concentrations of isolated fish remains, especially in the first 3 centimetres of this siltstone layer. The large white spot at 2.5 cm is a coprolite fragment.
Data from: Holocene lake phosphorus species and primary producers reflect catchment processes in a small, temperate lake
<p>This palaeo data set consists of a Holocene record from a small, temperate lake (Lake Fuglsø, Denmark). It comprises radiocarbon (<sup>14</sup>C)-dating, pollen, X-ray fluorescence scanning, carbon and nitrogen (contents and stable isotopes), phosphorus (P) pools (from sequential P extraction and <sup>31</sup>P nuclear magnetic resonance spectroscopy), pigment, diatom, and plant macrofossil data. Our multi-proxy palaeolimnological study aimed to investigate how natural processes and anthropogenic land-use changes have affected sedimentary P forms and primary producers. We found three periods of human impact: (1) low disturbance from domestic grazing during the Early/Mid Neolithic (~3600 – ~2600 BC), (2) higher disturbance because of animal husbandry and some grain cultivation during the Late Bronze and Pre-Roman Iron Age (~800 BC – AD ~100) and (3) strong disturbance caused by domestic grazing, intensified crop cultivation and, in particular, by retting of fibre plants during the Middle Ages and Renaissance (AD ~1000 – ~1700). Cultural eutrophication during the latter phase caused unprecedented changes in the lake, including altered species composition, high production and strongly accelerated sediment accumulation rates. Generally, catchment deforestation was related to elevated proportions of metal (iron, aluminium, calcium)-bound P forms in the sediment, while high tree cover correlated with elevated proportions of P forms associated with organic material ("organic" P, humic-bound P, refractory organic P) and loosely bound P. During phases with forest in the catchment, silicon (Si) inputs to the lake were insufficient and diatom frustules were mostly absent in the sediments. In contrast, diatoms thrived in the lake when the landscape was open and erosional Si influx was high. This study is the first to show long-term (~eight millennia) and recurring Si limitation of diatoms, a finding that may explain the absence of diatoms in sediment records of other sites too. In summary, human land-use with preceding deforestation accelerated the transport of nutrients and elements from the terrestrial to the aquatic environment, leading to substantial and irreversible changes in Lake Fuglsø. Our study is a good example of the tight links between catchment processes and lake status, indicating that catchment dynamics should be considered in lake restoration projects, particularly for lowland lakes with high catchment:lake area ratios.</p>
Fig. 1 in Genetic And Morphological Variability Of Small Vendace (Coregonus Albula (Linnaeus, 1758)) Population In Three Latvian Lakes
Fig. 1. The location of sampling sites. - Lake Sventes, Lake Nirzas and Lake Rāznas.
Data from: Holocene lake phosphorus species and primary producers reflect catchment processes in a small, temperate lake
Open the record for dataset details and reuse information.
Does salinization impact long-term Daphnia assemblage dynamics? Evidence from the sediment egg bank in a small hard-water lake
<p>Salinization of freshwater ecosystems threatens global aquatic biodiversity. There is a need for studies that follow populations <i>in situ </i>during salinization to understand the effects on species and ecosystems. We follow 170 years of <i>Daphnia </i>dynamics in the sediment ephippia archive of a small urban lake near St. Paul, Minnesota, to characterize effects of severe recent salinization on lake<i> Daphnia</i>. We found modest changes in the flux of ephippia in this lake; all three key <i>Daphnia </i>functional groups remained in the assemblage throughout the period of salinization. Reconstruction of the size distribution of <i>D. pulicaria </i>demonstrated that predation pressure by fish may not have increased for the largest and most susceptible member of the assemblage despite cultural meromixis. Our findings highlight that in hardwater lakes, the effects of salinization are nuanced and require further investigation to better understand overall impacts of salinization on lake <i>Daphnia </i>assemblages.</p>
Distribution. EC Madagascar, confined to two subpopulations on the shores of Lake Alaotra, a small one on the NW part of the lake around the Belempona Peninsula and a larger one in the adjoining marshlands along the lake's SW shores. in Lemuridae
Distribution. EC Madagascar, confined to two subpopulations on the shores of Lake Alaotra, a small one on the NW part of the lake around the Belempona Peninsula and a larger one in the adjoining marshlands along the lake's SW shores.
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.
Distribution. Restricted to three small isolated areas of S Siberia (NE Buryatia and N Zabaykalsky Krai): N Barguzin River, Lake Baunt, and Lower Muya River hollows. in Cricetidae
Distribution. Restricted to three small isolated areas of S Siberia (NE Buryatia and N Zabaykalsky Krai): N Barguzin River, Lake Baunt, and Lower Muya River hollows.
Distribution. Restricted to three small isolated areas in the lower Amur River Basin of Russian Far East (Upper Bureya River Depression, Chukchagyr-Evoron lakes Depression, adjacent parts of Amgun River Valley, and Upper Zeya River Depression). in Cricetidae
Distribution. Restricted to three small isolated areas in the lower Amur River Basin of Russian Far East (Upper Bureya River Depression, Chukchagyr-Evoron lakes Depression, adjacent parts of Amgun River Valley, and Upper Zeya River Depression).
Distribution. Restricted to the Kahuzi Mts in E DR Congo; confined to a small montane region W of Lake Kivu between Lwiro and Mt Kahuzi (1700-3300 m). Probably widely distributed in undisturbed areas above 2000 m. in Soricidae
Distribution. Restricted to the Kahuzi Mts in E DR Congo; confined to a small montane region W of Lake Kivu between Lwiro and Mt Kahuzi (1700-3300 m). Probably widely distributed in undisturbed areas above 2000 m.
Subspecies and Distribution. C.e.erythrotisWaterhouse,1838—mountainousareasinC&SBiokoI(EquatorialGuinea). C. e. camerunensis Hayman, 1940 — SE Nigeria (E of lower Cross River) and NW Cameroon (N of lower Sanaga River), also in a small areajust S of the Sanaga River, near its mouth, between Tinaso and Lake Tisongo. in Cercopithecidae
Subspecies and Distribution. C.e.erythrotisWaterhouse,1838—mountainousareasinC&SBiokoI(EquatorialGuinea). C. e. camerunensis Hayman, 1940 — SE Nigeria (E of lower Cross River) and NW Cameroon (N of lower Sanaga River), also in a small areajust S of the Sanaga River, near its mouth, between Tinaso and Lake Tisongo.
Distribution. Now restricted to the Channel Country of SW Queensland and the Lake Eyre Basin in NE South Australia. Descriptive notes. Head-body 95-120 mm, tail 105-160 mm, ear 23-29 mm, hindfoot 32-37 mm; weight 30-50 g. The Fawn Hopping Mouse has body form typical of hopping mice, with very long hindfeet, long tail with distal brush of longer hairs, very long ears, and large protruberant eyes. Dorsal fur is of variable color, from pale pinkish fawn to gray; ventral fur white. Unlike most other hopping mice, it has no throat pouch, but males have a glandular area of naked skin on the chest. Habitat. Occurs in low shrublands and tussock grasslands on stony ("gibber") plains and claypans. Shows marked habitat segregation from the Dusky Hopping Mouse (N. fuscus), which is closely associated with sandy substrates. Food and Feeding. The Fawn Hopping Mouse is mostly granivorous, but also eats other plant material (stems, leaves) and occasionally invertebrates. It uses succulent, salt-adapted plants around edges of claypans as a source of water. Breeding. Reproduction is probably largely opportunistic and aseasonal, with high reproductive output from near-continuous breeding after periods of high rainfall; reported littersize is 1-5, most commonly three; gestation period 38-43 days for nonlactating females. Females may mature later than other hopping mice, with reproductive maturity reached at about six months. Activity patterns. Terrestrial and nocturnal. Fawn Hopping Mice shelter during day in burrow systems that are typically simpler and shallower than those of other hopping mice. Movements, Home range and Social organization. Fawn Hopping Mice generally live singly or in small groups; typically uncommon within range, but population density may increase by an order of magnitude following periods of high rainfall. Status and Conservation. Classified as Near Threatened on The IUCN Red List. The Fawn Hopping Mouse has shown marked decline in range (estimated at greater than 50%), and presumably population size, since European settlement of Australia. This is mostlikely due to predation by the introduced house cat and Red Fox (Vulpes vulpes), and to habitat degradation associated with pastoralism. Bibliography. Brazenor (1934), Burbidge et al. (2008), Finlayson (1939), Gould (1853), Jackson & Groves (2015), Murray et al. (1999), Ogilby (1892), Thomas (1921h), Van Dyck & Strahan (2008), Waite (1898), Watts & Aslin (1981), Woinarski et al. (2014), Wood Jones (1925). in Muridae
Distribution. Now restricted to the Channel Country of SW Queensland and the Lake Eyre Basin in NE South Australia. Descriptive notes. Head-body 95-120 mm, tail 105-160 mm, ear 23-29 mm, hindfoot 32-37 mm; weight 30-50 g. The Fawn Hopping Mouse has body form typical of hopping mice, with very long hindfeet, long tail with distal brush of longer hairs, very long ears, and large protruberant eyes. Dorsal fur is of variable color, from pale pinkish fawn to gray; ventral fur white. Unlike most other hopping mice, it has no throat pouch, but males have a glandular area of naked skin on the chest. Habitat. Occurs in low shrublands and tussock grasslands on stony ("gibber") plains and claypans. Shows marked habitat segregation from the Dusky Hopping Mouse (N. fuscus), which is closely associated with sandy substrates. Food and Feeding. The Fawn Hopping Mouse is mostly granivorous, but also eats other plant material (stems, leaves) and occasionally invertebrates. It uses succulent, salt-adapted plants around edges of claypans as a source of water. Breeding. Reproduction is probably largely opportunistic and aseasonal, with high reproductive output from near-continuous breeding after periods of high rainfall; reported littersize is 1-5, most commonly three; gestation period 38-43 days for nonlactating females. Females may mature later than other hopping mice, with reproductive maturity reached at about six months. Activity patterns. Terrestrial and nocturnal. Fawn Hopping Mice shelter during day in burrow systems that are typically simpler and shallower than those of other hopping mice. Movements, Home range and Social organization. Fawn Hopping Mice generally live singly or in small groups; typically uncommon within range, but population density may increase by an order of magnitude following periods of high rainfall. Status and Conservation. Classified as Near Threatened on The IUCN Red List. The Fawn Hopping Mouse has shown marked decline in range (estimated at greater than 50%), and presumably population size, since European settlement of Australia. This is mostlikely due to predation by the introduced house cat and Red Fox (Vulpes vulpes), and to habitat degradation associated with pastoralism. Bibliography. Brazenor (1934), Burbidge et al. (2008), Finlayson (1939), Gould (1853), Jackson & Groves (2015), Murray et al. (1999), Ogilby (1892), Thomas (1921h), Van Dyck & Strahan (2008), Waite (1898), Watts & Aslin (1981), Woinarski et al. (2014), Wood Jones (1925).
Mapping global lake dynamics reveals the emerging roles of small lakes: code and data
<p>This repository contains the relevant code and data for the paper <strong>Mapping global lake dynamics reveals the emerging roles of small lakes (</strong><a href="http://dx.doi.org/10.1038/s41467-022-33239-3">https://www.nature.com/articles/s41467-022-33239-3</a><strong>)</strong>.</p> <p>Specifically, the <strong>U-Net.zip</strong> file includes the associated codes for segmenting global lakes by using the U-Net model, and the labels used in this process. The <strong>GLAKES.zip</strong> file includes the GLAKES lake polygon product (.gdb & .shp) and the corresponding water probability-weighted area of GLAKES lakes during the three periods (1984-1999, 2000-2009, 2010-2019). Please refer to the README file in both the <strong>U-Net.zip</strong> and the <strong>GLAKES.zip </strong>file for more detailed information.</p>
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.