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59 results for “artificial habitat”
Habitat-driven vulnerability to nest predation in Arctic-breeding plovers based on artificial nest experiment and real shorebird nest monitoring – Survival dataset
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Greater functional similarity in mobile compared to sessile assemblages colonizing artificial coastal habitats
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Data from: The distribution of plants and seed dispersers in response to habitat fragmentation in an artificial island archipelago
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Data From: An artificial habitat increases the reproductive fitness of a range-shifting species within a newly colonized ecosystem
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Data from: Detection of vertebrates from natural and artificial inland water bodies in a semi-arid habitat using eDNA from filtered, swept and sediment samples
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Data from: Artificial light at night confounds broad-scale habitat use by migrating birds
With many of the world's migratory bird populations in alarming decline, broad-scale assessments of responses to migratory hazards may prove crucial to successful conservation efforts. Most birds migrate at night through increasingly light-polluted skies. Bright light sources can attract airborne migrants and lead to collisions with structures, but might also influence selection of migratory stopover habitat and thereby acquisition of food resources. We demonstrate, using multi-year weather radar measurements of nocturnal migrants across the northeastern U.S., that autumnal migrant stopover density increased at regional scales with proximity to the brightest areas, but decreased within a few kilometers of brightly-lit sources. This finding implies broad-scale attraction to artificial light while airborne, impeding selection for extensive forest habitat. Given that high-quality stopover habitat is critical to successful migration, and hindrances during migration can decrease fitness, artificial lights present a potentially heightened conservation concern for migratory bird populations.
Data from: Distribution of the invasive Caprella mutica Schurin, 1935 and native Caprella linearis (Linnaeus, 1767) on artificial hard substrates in the North Sea: separation by habitat
Studying offshore natural and artificial hard substrates in the southern North Sea (51ºN–57ºN/1ºW–9ºE), the invasive introduced Japanese skeleton shrimp Caprella mutica Schurin, 1935 was found to co-exist with the native Caprella linearis (Linnaeus, 1767) only on near-shore locations that had an intertidal zone (e.g., wind farm foundations). In contrast, on far offshore and strictly subtidal locations, such as shipwrecks and rocky reefs, only C. linearis was found. Based on these exploratory observations, we hypothesised that artificial structures that are only subtidal are inhabited exclusively by C. linearis, and never by C. mutica. To test this hypothesis and understand factors driving each species' habitat preferences, habitat suitability models were constructed using generalised additive models, based on samples collected in 2013–2015 from offshore gas platforms, buoys, shipwrecks, and rocky reefs and combined with data from other published and unpublished surveys (2001–2014). The models showed that the presence of C. mutica is explained by the availability of intertidal and floating hard substrates, suspended particulate matter density (SPM), mean annual sea surface temperature, salinity, and current velocity. The C. linearis model included subtidal hard substrates, SPM, salinity, temperature, and current velocity. The modelled distributions showed a significant difference, demonstrating that C. linearis' habitat preference does not fully overlap with that of C. mutica. Thus, the native and alien Caprella species are likely to be able to co-exist in the North Sea.
Fig. 10 in Demographic data on a stag beetle (Lucanus cervus) population self-established in an artificial suburban habitat
Fig. 10. Yearly number of stag beetles found dead by predation at the Jagersveld CMR site during the period 2001- 2023. Areas in grey refer to predation by Corvids, areas in yellow to predation by hedgehogs. The annual sex-ratio measured on these beetle remains is indicated, as is the yearly total number of beetles killed by predators and the total number of natural deaths.
Fig. 9 in Demographic data on a stag beetle (Lucanus cervus) population self-established in an artificial suburban habitat
Fig. 9. Variation, as a function of year, of the mean and standard error of head width (KB) of males found dead at the Jagersveld CMR site. Numbers indicate the size of the samples, and letters and colors indicate samples not significantly differing in size from each other at the P = 0.05 threshold, by using the non-parametric Kruskal-Wallis test for multiple comparisons. Samples of years 1924 and 2021 were excluded from the K-W analysis.
Fig. 8 in Demographic data on a stag beetle (Lucanus cervus) population self-established in an artificial suburban habitat
Fig. 8. Box plots of total length (TL) of stag beetles measured in the order of their first appearance at the Jagersveld site during the capture-mark-recapture exercise of 2007. Median, quartiles and extremes of male sizes over successive weeks and of female sizes over successive ten-day periods.
Fig. 6 A-B in Demographic data on a stag beetle (Lucanus cervus) population self-established in an artificial suburban habitat
Fig. 6 A-B. Survivorship curves of marked male stag beetles during (A) the 2001 and (B) 2007 CMR exercises, in function of death as end event. Kaplan-Meyer step-curves with 95% upper and lower confidence bounds. The arrows indicate the medians of the known life span. A Weibull curve is drawn over the K-M curve. C: illustrating the lack of statistical difference between the 2001 and 2007 K-M curves.
Fig. 4 in Demographic data on a stag beetle (Lucanus cervus) population self-established in an artificial suburban habitat
Fig. 4. Cumulative number of new individuals at the Jagersveld site during the CMR sessions of 2001 and 2007. (a): appearance of the first males. (b): geometric increase of new individuals during a short period. The graphs in the right insets show this increase in semi-logarithmic coordinates. (i): inflection point. (c): more regular increase of new individuals until reaching (d) a plateau (p). The increase of new females was more progressive.
Fig. 3 in Demographic data on a stag beetle (Lucanus cervus) population self-established in an artificial suburban habitat
Fig. 3. Calendar of male capture and recapture histories at the Jagersveld site. The marked individuals are sorted by date of first capture and by known duration of longevity. 1: captured. 0: not encountered in the interval where the individual was known to be alive. +: found dead by predation on the sampling site. *: natural death. MNA: minimum number known alive.
Fig. 5 in Demographic data on a stag beetle (Lucanus cervus) population self-established in an artificial suburban habitat
Fig. 5. Distribution of the number of males confirmed to be still alive, as a function of the number of days elapsed since they were marked during the 2001 and 2007 CMR exercises. The construction of the curves is based on the first two columns of Table 1 and is limited to 23 days for the year 2007.
Fig. 1 in Demographic data on a stag beetle (Lucanus cervus) population self-established in an artificial suburban habitat
Fig. 1. Aerial view of part of the locality of Boitsfort, a suburb in the south-east of the city of Brussels, with, encircled in yellow, the stag beetle brood sites as they were known for at least the years 2000-2010. Larval sites were (and are) mainly located outside densely wooded plots, and even in the alignments of ornamental cherry trees along certain avenues. Note also the dispersion of these sites, whose circle size do not prejudge the size of their beetle population. Orthophoto plan from UrbIS datastore.brussels.
Fig. 7 in Demographic data on a stag beetle (Lucanus cervus) population self-established in an artificial suburban habitat
Fig. 7. Daily estimates of the number of beetles at the Jagersveld site in 2001 and 2007 according to the POPAN formulation of the Jolly-Seber method, under the acceptance of constant survival and capture probabilities over time. Minimum daily number of known survivors (MNA). Rainy periods and, for 2001, stormy evening episodes, are figured at the bottom of the graphs.
Fig. 2. A in Demographic data on a stag beetle (Lucanus cervus) population self-established in an artificial suburban habitat
Fig. 2. A, The ramp to the playground of the Jagersveld school, with its central staircase in 2001. B, The palisade of beams of the east side of the ramp in its 2007 state, however photographed in 2013, the staircase having been removed in the meantime. C, The earthen platform at the top of the ramp in 2002, with the alignment of short beams separating it from the concrete of the ramp. D, The same platform fenced and overgrown with maple saplings, as viewed in 2022. E - F, Stag beetle larvae and a pupa found in 2005 when some of the beams were replaced. G - H, damage to the paling, west side and east side, in 2021. © E and F, courtesy Olivier Beck.
Data from: Do positive interactions between marine invaders increase likelihood of invasion into natural and artificial habitats?
<p>Positive species interactions such as facilitation are important for enabling species to persist, especially in stressful conditions, and the nature and strength of facilitation varies along physical and biological gradients. Expansion of coastal infrastructure is creating hotspots of invasive species which can spillover into natural habitats, but the role of positive species interactions associated with biological invasions remains understudied. Theory suggests that stronger biotic pressure in natural habitats inhibits invasion success. In space-limited marine systems, sessile organisms can overcome this limiting resource by settling as an epibiont on a substrate organism - basibiont. Using a series of spatially extensive surveys, we explored the role of invasive and native basibionts in providing habitat for other invasive and native epibionts, and tested whether environmental context (i.e. if the receiving habitat was natural or artificial), altered ecological outcomes. Overall, provision of space by basibionts was more important for invasive epibionts than for native epibionts but was dependent on the environmental context. Invasive basibionts facilitated invasive epibionts in natural habitats, and appeared to be more important for native epibionts in artificial habitats respectively. Native basibionts facilitated invasive, but not native epibionts in both natural and artificial habitats. These results advance our understanding of facilitation and highlight the idiosyncratic nature of biofouling and epibiosis, and the potentially important influence of environmental context. The degree to which native habitat-forming species vs. invasive habitat-forming species either do or do not facilitate other native or non-native species is a rich area for investigation. Experimental work is required to disentangle the processes underpinning these patterns.</p>
Data from: A comparative study on genetic effects of artificial and natural habitat fragmentation on Loropetalum chinense (Hamamelidaceae) in Southeast China
Elucidating the demographic and landscape features that determine the genetic effects of habitat fragmentation has become fundamental to research in conservation and evolutionary biology. Land-bridge islands provide ideal study areas for investigating the genetic effects of habitat fragmentation at different temporal and spatial scales. In this context, we compared patterns of nuclear microsatellite variation between insular populations of a shrub of evergreen broad-leaved forest, Loropetalum chinense, from the artificially created Thousand-Island Lake (TIL) and the Holocene-dated Zhoushan Archipelago of Southeast China. Populations from the TIL region harboured higher levels of genetic diversity than those from the Zhoushan Archipelago, but these differences were not significant. There was no correlation between genetic diversity and most island features, excepting a negative effect of mainland–island distance on allelic richness and expected heterozygosity in the Zhoushan Archipelago. In general, levels of gene flow among island populations were moderate to high, and tests of alternative models of population history strongly favoured a gene flow-drift model over a pure drift model in each region. In sum, our results showed no obvious genetic effects of habitat fragmentation due to recent (artificial) or past (natural) island formation. Rather, they highlight the importance of gene flow (most likely via seed) in maintaining genetic variation and preventing inter-population differentiation in the face of habitat 'insularization' at different temporal and spatial scales.
Aedes albopictus has not become the dominant species in artificial container habitats in a temperate forest more than a decade after establishment
<p><i>Aedes albopictus </i>(Skuse) is one of the most invasive species globally, and has led to rapid declines and local extirpations of resident mosquitoes where it becomes established. A potential mechanism behind these displacements is the superior competitive ability of <i>Ae. albopictus</i> in larval habitats. Research on the context-dependent nature of competitive displacement predicts that <i>Ae. albopictus</i> will not replace native <i>Aedes triseriatus </i>(Say) in treeholes but could do so in artificial container habitats. <i>Ae. albopictus</i> remains rare in temperate treeholes but less is known about how <i>Ae. albopictus</i> fares in artificial containers in forests. Tyson Research Center (TRC) is a field station composed of mostly oak-hickory forest located outside Saint Louis, MO. The container community has been studied regularly at TRC since 2007 with permanently established artificial containers on the property since 2013. <i>Ae. albopictus</i> was detected each year these communities were sampled; however, its abundance remains low and it fails to numerically dominate other species in these communities. We present data that show <i>Ae. albopictus</i> numbers have not increased in the last decade. We compare egg counts from 2007 and 2016 and combine larval sample data from 2012-2017.We present average larval densities and prevalence of <i>Ae. albopictus</i> and two competitors, <i>Ae. triseriatus</i> and <i>Aedes japonicus </i>(Theobald) as well as monthly averages by year. These data highlight a circumstance in which <i>Ae. albopictus</i> fails to dominate the <i>Aedes</i> community despite it doing so in more human-impacted habitats. We present hypotheses for these patterns based upon abiotic and biotic environmental conditions.</p>
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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.