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18 results for “Habitat Degradation”
Figure 2 in Impacts of anthropogenic activities and habitat degradation on breeding waterbirds
Figure 2. Distribution and observation frequency of urbanization, industrialization, pollution, overgrazing, disturbance, and illegal reed cutting and burning threats in 2002.
Data from: Dietary resilience of coral reef fishes to habitat degradation
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A meta-analysis exploring associations between habitat degradation and Neotropical bat virus prevalence and seroprevalence
<p>Habitat degradation can increase zoonotic disease risks by altering infection dynamics in wildlife and increasing wildlife–human interactions. Bats are an important taxonomic group to consider these effects, because they harbour many relevant zoonotic viruses and have species- and context-dependent responses to degradation that could affect zoonotic virus dynamics. Yet our understanding of the associations between habitat degradation and bat virus prevalence and seroprevalence are limited to a small number of studies, which often differ in the bats or viruses sampled, the study region, and methodology. To develop a broad understanding of the associations between bat viruses and habitat degradation, we conducted an initial phylogenetic meta-analysis that combines published prevalence and seroprevalence ("(sero)prevalence") with remote-sensing habitat degradation data. Our dataset includes 588 unique records of (sero)prevalence across 16 studies, 64 bat species, and five virus families. We quantified the overall strength and direction of the relationship between habitat degradation and bat virus outcomes and tested how this relationship is moderated by the time between habitat degradation and bat sampling and by ecological traits of bat hosts while controlling for phylogenetic nonindependence among bat species. We found no effect of degradation on prevalence overall, although a weak effect may exist when forest loss occurs the year prior to bat sampling. In contrast, we detected a negative but weak association between degradation and seroprevalence overall that was strengthened when forest loss occurred the year prior to bat sampling. No bat traits that we investigated interacted with habitat degradation to impact virus outcomes, suggesting observed trends are independent of these traits. Biases in our initial dataset highlight opportunities for future work; prevalence was highly zero-inflated, and seroprevalence was dominated by <em>Desmodus rotundus</em> and rabies virus. These findings and subsequent analyses will improve our understanding of how global change affects host–pathogen dynamics.</p>
Data from: Trends in habitat quality and habitat degradation within terrestrial protected areas
<p>Please see the paper<strong> "Trends in habitat quality and habitat degradation within terrestrial protected areas"</strong> for the definition of habitat quality, habitat degradation and different threats.</p> <p>This dataset describes global habitat quality and degradation for 2020, with a resolution of 250 m. Values of habitat quality and total habitat degradation can be used directly. <strong>Of note, values of habitat degradation caused by each threat should be multiplied by the relative threat weights before use.</strong> The details are as follows:</p> <ol> <li>"quality_c_2020.tif" represents habitat quality.</li> <li>"deg_sum_c_2020.tif" represents total habitat degradation which is caused by all 5 threats.</li> <li>"deg_sum_c_NonIrriCrp_2020.tif" represents habitat degradation caused by non-irrigated cropland, and should be multiplied by 0.2145 before use.</li> <li>"deg_sum_c_IrriCrp_2020.tif" represents habitat degradation caused by irrigated cropland, and should be multiplied by 0.2292 before use.</li> <li>"deg_sum_c_CrpVeg_2020.tif" represents habitat degradation caused by mosaic cropland-vegetation, and should be multiplied by 0.1623 before use.</li> <li>"deg_sum_c_VegCrp_2020.tif" represents habitat degradation caused by mosaic vegetation-cropland, and should be multiplied by 0.0541 before use.</li> <li>"deg_sum_c_Urban_2020.tif" represents habitat degradation caused by urban areas, and should be multiplied by 0.3400 before use.</li> </ol> <p>Besides, "InputData_forR.zip" provides data on protected-area-level habitat quality and habitat degradation, which is for statistical analyses by R in the paper "Trends in habitat quality and habitat degradation within terrestrial protected areas".</p>
A meta-analysis exploring associations between habitat degradation and Neotropical bat virus prevalence and seroprevalence
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Data from: Variation in the impact of non-native seaweeds along gradients of habitat degradation: a meta-analysis and an experimental test
Biological invasions are acknowledged among the main drivers of global changes in biodiversity. Despite compelling evidence of species interactions being strongly regulated by environmental conditions, there is a dearth of studies investigating how the effects of non-native species vary among areas exposed to different anthropogenic pressures. Focusing on marine macroalgae, we performed a meta-analysis to test whether and how the direction and magnitude of their effects on resident communities and species varies in relation to cumulative anthropogenic impact levels. The relationship between human impact levels and non-native species impact intensity emerged only for a reduced subset of the response variables examined. Yet, there was a trend for the effects of non-native species on community biomass and abundance and on species abundance to become less negative at heavily impacted sites. By contrast, the magnitude of negative effects of seaweed on community evenness tended to increase with human impact levels. The hypothesis of decreasing severity of invader' impacts along a gradient of habitat degradation was also tested experimentally at a regional scale by comparing the effects of the removal of non-native alga, Caulerpa cylindracea, on resident assemblages among rocky reefs exposed to different anthropogenic pressures. Assemblages at urban and pristine site did not differ when invaded, but did so when C. cylindracea was removed. Our results suggest that, despite the generally weak relationship between human impacts levels and non-native species impacts, more negative impacts can be expected in less stressful environments (i.e. less degraded or pristine sites), where competitive interactions are presumably the driving force structuring resident communities. Implementing strategies for controlling the establishment of non-native seaweeds should be, thus, considered a priority for preserving biodiversity in relatively pristine areas. On the other hand, control of invaders at degraded sites could be warranted to lessen their role as propagule sources.
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).
The first comprehensive revision of all the species attributed to Melomys led J. I. Menzies in 1996 to resurrect the genus Paramelomys and to redefine its morphologicallimits and species content. Menzies created P. gressitti as a new species belonging to a group displaying morphological similarities and including also P. lorentzii and P. moncktoni. Monotypic Distribution. E New Guinea. Descriptive notes. Head-body 135-162 mm, hindfoot 30-34 mm; no specific data are available for body weight. Gressitt's Mosaic-tailed Rat is a medium-sized Paramelomys with a soft, thick and woolly pelage, a long narrow foot, and a tail with three hairs per scale. It exhibits a medium-sepia dorsal pelage and a gray-buff ventral one. Tail is slightly shorter (99%) than head-body length. The skull has a narrow zygomatic plate. Habitat. Moist tropical mountain forest between 2300 m and 2400 m. Food and Feeding. No information. Breeding. No information. Activity patterns. Gressitt's Mosaic-tailed Rat is terrestrial. Movements, Home range and Social organization. No information. Status and Conservation. Classified as Endangered on The IUCN Red List owing to its small geographic range (less than 3500 km?*) and the destruction ofits habitat by mining and logging activities. The major threat to Gressitt's Mosaic-tailed Rat is ongoing habitat degradation caused by nearby human populations; habitat on Mount Kandy has been destroyed by gold-miners and wood-cutters. Bibliography. Menzies (1996). in Muridae
The first comprehensive revision of all the species attributed to Melomys led J. I. Menzies in 1996 to resurrect the genus Paramelomys and to redefine its morphologicallimits and species content. Menzies created P. gressitti as a new species belonging to a group displaying morphological similarities and including also P. lorentzii and P. moncktoni. Monotypic Distribution. E New Guinea. Descriptive notes. Head-body 135-162 mm, hindfoot 30-34 mm; no specific data are available for body weight. Gressitt's Mosaic-tailed Rat is a medium-sized Paramelomys with a soft, thick and woolly pelage, a long narrow foot, and a tail with three hairs per scale. It exhibits a medium-sepia dorsal pelage and a gray-buff ventral one. Tail is slightly shorter (99%) than head-body length. The skull has a narrow zygomatic plate. Habitat. Moist tropical mountain forest between 2300 m and 2400 m. Food and Feeding. No information. Breeding. No information. Activity patterns. Gressitt's Mosaic-tailed Rat is terrestrial. Movements, Home range and Social organization. No information. Status and Conservation. Classified as Endangered on The IUCN Red List owing to its small geographic range (less than 3500 km?*) and the destruction ofits habitat by mining and logging activities. The major threat to Gressitt's Mosaic-tailed Rat is ongoing habitat degradation caused by nearby human populations; habitat on Mount Kandy has been destroyed by gold-miners and wood-cutters. Bibliography. Menzies (1996).
Supplementary material 1 from: Pérez-Luque AJ, Zamora R, Bonet FJ, Pérez-Pérez R (2015) Dataset of MIGRAME Project (Global Change, Altitudinal Range Shift and Colonization of Degraded Habitats in Mediterranean Mountains). PhytoKeys 56: 61-81. https://doi.org/10.3897/phytokeys.56.5482
Table S1: Explanation note: Information about transects of the project. Elevation in m a.s.l. Type: AM = Altitudinal migration; FO = Forest; MH = Marginal Habitat. Subtype: AC-e: Abandoned Cropland: edge; AC-i: Abandoned Cropland: inside; Pp-e: Pine plantations: edge; Pp-i: Pine plantations: inside; TE: Treeline Ecotone. Locality: CA = Robledal de Cáñar; SJ = Robledal de San Juan.
Habitat geometry in artificial microstructure affects bacterial and fungal growth, interactions, and substrate degradation 2nd part
<p>Microhabitat conditions determine the magnitude and speed of microbial processes but have been challenging to investigate. In this study we used microfluidic devices to determine the effect of the spatial distortion of a pore space on fungal and bacterial growth<i>,</i> interactions, and substrate degradation. The devices contained channels differing in bending angles and order. Sharper angles reduced fungal and bacterial biomass, especially when angles were repeated in the same direction. Substrate degradation was only decreased by angles when fungi and bacteria were grown together. Investigation at the cellular scale suggests that this was caused by fungal habitat modification, which branched in sharp and repeated turns, blocking the dispersal of bacteria and the substrate. Our results demonstrate how the geometry of microstructures can influence microbial activity. This can be transferable to soil pore spaces, where spatial occlusion and microbial feedback on microstructures is thought to explain organic matter stabilization.</p>
Habitat geometry in artificial microstructure affects bacterial and fungal growth, interactions, and substrate degradation 2nd part
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Data from: Variation in the impact of non-native seaweeds along gradients of habitat degradation: a meta-analysis and an experimental test
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Figure 3 in Impacts of anthropogenic activities and habitat degradation on breeding waterbirds
Figure 3. Distribution of the total number of breeding bird species and waterbird species per UTM grid in 2002 and 2006.
Figure 4 from: Pérez-Luque AJ, Zamora R, Bonet FJ, Pérez-Pérez R (2015) Dataset of MIGRAME Project (Global Change, Altitudinal Range Shift and Colonization of Degraded Habitats in Mediterranean Mountains). PhytoKeys 56: 61-81. https://doi.org/10.3897/phytokeys.56.5482
Figure 4 - Diagram of integration of the dataset within Information System of Sierra Nevada Global Change Observatory (http://obsnev.es/linaria.html). Field data were recorded with Smartphone devices (see Pérez-Pérez et al. 2013). After a validation process (see Quality Control section) the occurrence and measurement data were accommodated to Darwin Core Archive and integrated into GBIF.
Figure 3 from: Pérez-Luque AJ, Zamora R, Bonet FJ, Pérez-Pérez R (2015) Dataset of MIGRAME Project (Global Change, Altitudinal Range Shift and Colonization of Degraded Habitats in Mediterranean Mountains). PhytoKeys 56: 61-81. https://doi.org/10.3897/phytokeys.56.5482
Figure 3 - Sampling Design. a Altitudinal migration hypothesis. At each study site, from the forest edge to treeline ecotone, we sampled each 25 m of elevation b Colonization of marginal habitat hypothesis. Transects were located on three habitat types: Forests (brown circles), Forest Edges (red squares) and Inside Marginal Habitats (blue triangles).
Figure 2 from: Pérez-Luque AJ, Zamora R, Bonet FJ, Pérez-Pérez R (2015) Dataset of MIGRAME Project (Global Change, Altitudinal Range Shift and Colonization of Degraded Habitats in Mediterranean Mountains). PhytoKeys 56: 61-81. https://doi.org/10.3897/phytokeys.56.5482
Figure 2 - Distribution of Quercus pyrenaica forests in Iberian Peninsula (a). Sierra Nevada harbours eight populations of Quercus pyrenaica clustered into three groups (different colours). We selected two study sites: Robledal de Cañar (c) and Robledal San Juan (d). Colour Orthophotography of 2009 from Regional Ministry of the Environment, Regional Government of Andalusia.
Figure 1 from: Pérez-Luque AJ, Zamora R, Bonet FJ, Pérez-Pérez R (2015) Dataset of MIGRAME Project (Global Change, Altitudinal Range Shift and Colonization of Degraded Habitats in Mediterranean Mountains). PhytoKeys 56: 61-81. https://doi.org/10.3897/phytokeys.56.5482
Figure 1 - Schematic representation of the two main hypothesis of the project: altitudinal migration (a) and colonization of marginal areas (b) of Quercus pyrenaica forests.
FIGURE 1. Chusquea heterophylla. A–B. Habitat and habit. C. Young culm showing extravaginal branching and developing branches pushing the culm leaf apices away from the culm. D. Developed subequal branches and culm leaves degrading with age. E in Morphological, geographic and ecological evidence support a new species of Chusquea subg. Swallenochloa (Poaceae, Bambusoideae, Bambuseae) from Parque Nacional do Caparaó, Brazil
FIGURE 1. Chusquea heterophylla. A–B. Habitat and habit. C. Young culm showing extravaginal branching and developing branches pushing the culm leaf apices away from the culm. D. Developed subequal branches and culm leaves degrading with age. E. Foliage leaf branches with synflorescences. (Photos by Evandro Pianissola. A Pico da Caledônia; B, D and E, Parque Nacional do Itatiaia; C Parque Estadual da Serra do Brigadeiro).
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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.