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43 results for “range boundaries”
Distribution. NW coastal Madagascar, restricted to the Sahamalaza Peninsula and the adjacent mainland; the biogeography of this area and the distribution pattern of the sympatric Blue-eyed Black Lemur (Eulemurflavifrons) make it likely that the boundaries of the range of the Sahamalaza Sportive Lemur are the Andranomalaza River in the N and the Maevarano Riverin the S. Field studies to determine the full extent of the distribution and that of neighboring Mittermeier's Sportive Lemur (L. mittermeiert) are underway. in Lepilemuridae
Distribution. NW coastal Madagascar, restricted to the Sahamalaza Peninsula and the adjacent mainland; the biogeography of this area and the distribution pattern of the sympatric Blue-eyed Black Lemur (Eulemurflavifrons) make it likely that the boundaries of the range of the Sahamalaza Sportive Lemur are the Andranomalaza River in the N and the Maevarano Riverin the S. Field studies to determine the full extent of the distribution and that of neighboring Mittermeier's Sportive Lemur (L. mittermeiert) are underway.
Distribution. Restricted and patchy range in NE Madagascar that includes the humid forest belt extending from the Marojejy Massif and the Andapa Basin to Maroantsetra; the Androranga River may be the NE distributional limit in the Tsaratanana Corridor, although further surveys are needed to confirm this, and the Antainambalana River in the Makira Forest protected area is currently regarded as the S boundary. Currently, Marojejy represents the N limit ofits distribution, although historic range maps suggest that it once occurred as far N as the Bemarivo River near Sambava. The NE distributional limit in Makira was only recently established, when a few groups were found in the Antohaka Lava Forest, but informal reports suggest that the unprotected Maherivaratra Forest, outside NE Makira, may also contain Silky Sifakas. in Indriidae
Distribution. Restricted and patchy range in NE Madagascar that includes the humid forest belt extending from the Marojejy Massif and the Andapa Basin to Maroantsetra; the Androranga River may be the NE distributional limit in the Tsaratanana Corridor, although further surveys are needed to confirm this, and the Antainambalana River in the Makira Forest protected area is currently regarded as the S boundary. Currently, Marojejy represents the N limit ofits distribution, although historic range maps suggest that it once occurred as far N as the Bemarivo River near Sambava. The NE distributional limit in Makira was only recently established, when a few groups were found in the Antohaka Lava Forest, but informal reports suggest that the unprotected Maherivaratra Forest, outside NE Makira, may also contain Silky Sifakas.
Distribution. CE Madagascar, the Mangoro and Onive rivers are the N limits of the present range, and the Rienana River in Andringitra National Park is the S boundary. The former distribution probably extended somewhat N and further S to the Manampatrana River, but populations in those regions appear to have been extirpated. in Indriidae
Distribution. CE Madagascar, the Mangoro and Onive rivers are the N limits of the present range, and the Rienana River in Andringitra National Park is the S boundary. The former distribution probably extended somewhat N and further S to the Manampatrana River, but populations in those regions appear to have been extirpated.
Data from: Influence of habitat availability and fire disturbance on the northern range boundary of eastern white cedar (Thuja occidentalis L.)
Aim <p>Non-climatic constraints on species northern range boundaries are often overlooked in attempts to predict climate-induced range shifts. Here, we examined the effects of habitat availability and fire disturbance on the distribution of eastern white cedar (<i>Thuja occidentalis</i> L.) at the northern boundary of its range.</p> Location <p>North-western Quebec, Canada (46-51° N and 74-79° W)</p> Methods <p>We used forest inventory data (<i>n</i>=4,987) to characterize white-cedar habitat based on edaphic and topographic conditions at sampled sites along a 600-km latitudinal gradient. Non-metric multidimensional scaling was used to assess habitat similarity of sites in the south, where white-cedar stands are abundant, and sites in the north, where white-cedar stands are rare. We constructed ensemble white cedar distribution models based on habitat variables in the south and compared ensemble forecast projections of white cedar in the north with observed occurrences to determine if habitat availability was limiting. We independently estimated the age of white-cedar stands and adjacent stands without white cedar along the gradient. ANOVA was performed to test the age difference between white-cedar and adjacent stands to determine if the location of white-cedar stands was influenced by disturbance, primarily stand-replacing fire.</p> Results <p>Habitat availability was not limiting the distribution of eastern white cedar at its northern range boundary. White cedar did not occupy most sites with suitable habitat in the north, suggesting that other factors prevent white cedar from establishing more stands northward. White-cedar stands were older than adjacent stands without white cedar all along the gradient, but the difference was more pronounced in the north. This suggests that white-cedar stands in the north are restricted to undisturbed areas.</p> Main conclusions <p>Fire disturbance, more than habitat availability, limits the distribution of white cedar at its northern range boundary. Projections of white cedar distribution under climate change that ignore fire could overestimate the ability of warming temperatures to extend its northern range limit.</p>
Data from: Spatial variation in bioclimatic relationships for a snow-adapted species along a discontinuous southern range boundary
<p>Documenting variation in the relationship between climate variables and species occurence at range boundaries can help reveal how species will respond to global climate change. We collected snowshoe hare (Lepus americanus) presence-absence data from snow-track surveys conducted in the U.S. states of Michigan and Wisconsin in winters from 2012-2014 at their southern range boundary in the region. A series of 125m transects were walked at each site within a week of fresh snowfall, and the presence or absence of snowshoe hare tracks on each transect was recorded. Data set also includes the variables mean 5-year snow cover duration, mean 5-year maximum temperature, and percentage forest cover at each site. Each variable was used in data analysis for the related paper to relate snowshoe hare occurrence to climate and land cover variables at the southern edge of their distribution. Snowshoe hares in the region occur in areas with longer snow cover duration and lower maximum temperatures but these relationships vary across the study area such that maximum temperature was positively correlated with snowshoe hare occurrence in the northern portion of the study area (Upper Peninsula of Michigan).</p>
Woodland Caribou demographic data and range boundaries
<p>As global climate change progresses, wildlife management will benefit from knowledge of demographic responses to climatic variation, particularly for species already endangered by other stressors. In Canada, climate change is expected to increasingly impact populations of threatened woodland caribou (<i>Rangifer tarandus caribou</i>) and much focus has been placed on how a warming climate has potentially facilitated the northward expansion of apparent competitors and novel predators. Climate change, however, may also exert more direct effects on caribou populations that are not mediated by predation. These effects include meteorological changes that influence resource availability and energy expenditure. Research on other ungulates suggests that climatic variation may have minimal impact on low-density populations such as woodland caribou because per-capita resources may remain sufficient even in "bad" years. We evaluated this prediction using demographic data from 21 populations in western Canada that were monitored for various intervals between 1994 and 2015. We specifically assessed whether juvenile recruitment and adult female survival were correlated with annual variation in meteorological metrics and plant phenology. Against expectations, we found that both vital rates appeared to be influenced by annual climatic variation. Juvenile recruitment was primarily correlated with variation in phenological conditions in the year prior to birth. Adult female survival was more strongly correlated with meteorological conditions and declined during colder, more variable winters. These responses may be influenced by the life history of woodland caribou, which reside in low-productivity refugia where small climatic changes may result in changes to resources that are sufficient to elicit strong demographic effects. Across all models, explained variation in vital rates was low, suggesting that other factors had greater influence on caribou demography. Nonetheless, given the declining trajectories of many woodland caribou populations, our results highlight the increased relevance of recovery actions when adverse climatic conditions are likely to negatively affect caribou demography.</p>
Data from: Quantitative genetic architecture at latitudinal range boundaries: reduced variation but higher trait independence
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Data from: Quantifying spatiotemporal occupancy dynamics and multi-year core-use areas at a species range boundary
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Data from: Distinct sources of gene flow produce contrasting population genetic dynamics at different range boundaries of a Choristoneura budworm
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Data from: Evolutionary dynamics of a rapidly receding southern range boundary in the threatened California Red-Legged Frog (Rana draytonii)
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Data from: Climate change surpasses land use change in the contracting range boundary of a winter-adapted mammal
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Data from: Influence of habitat availability and fire disturbance on the northern range boundary of eastern white cedar (Thuja occidentalis L.)
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Woodland Caribou demographic data and range boundaries
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Data from: Spatial variation in bioclimatic relationships for a snow-adapted species along a discontinuous southern range boundary
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Figure 4 from: Cuevas CC, Sanhueza R (2020) Geographic boundaries and natural history notes of the microendemic endangered frog Eupsophus migueli Formas, 1977 (Alsodidae) in the Mahuidanche Range, southern Chile. ZooKeys 929: 79-92. https://doi.org/10.3897/zookeys.929.35984
Figure 4 Scheme of the life history data of E. migueli (this paper) and E. altor. Data for E. altor were obtained from Núñez et al. (2012).
Figure 1 from: Cuevas CC, Sanhueza R (2020) Geographic boundaries and natural history notes of the microendemic endangered frog Eupsophus migueli Formas, 1977 (Alsodidae) in the Mahuidanche Range, southern Chile. ZooKeys 929: 79-92. https://doi.org/10.3897/zookeys.929.35984
Figure 1 A Distribution map of Eupsophus migueli. The red polygon corresponds to an updated distribution area of E. migueli, and it is formed by georeferenced landmarks including new records (this paper), old records (including the type locality, Mehuín, and nearby localities Queule and Pichicuyín) and other documented points (Méndez et al. 2005, Contreras 2014, Miranda 2015) B specimen of E. migueli from Colehual Alto.
Figure 3 from: Cuevas CC, Sanhueza R (2020) Geographic boundaries and natural history notes of the microendemic endangered frog Eupsophus migueli Formas, 1977 (Alsodidae) in the Mahuidanche Range, southern Chile. ZooKeys 929: 79-92. https://doi.org/10.3897/zookeys.929.35984
Figure 3 Habitat of Eupsophus migueliA, D native forest with anthropogenic disturbance in Boroa Norte 1 B pine monoculture with undergrowth habitat of Aristotelia chilensis in Boroa Norte 4 C, E native forest in El Socorro.
Figure 2 from: Cuevas CC, Sanhueza R (2020) Geographic boundaries and natural history notes of the microendemic endangered frog Eupsophus migueli Formas, 1977 (Alsodidae) in the Mahuidanche Range, southern Chile. ZooKeys 929: 79-92. https://doi.org/10.3897/zookeys.929.35984
Figure 2 Dorsal (capitals) and ventral (lowercase) patterns of pigmentation in Eupsophus migueli from different localities along its distribution range. A Dorsal pattern of dark brown (Socorro) a ventral white with longitudinal spots (El Socorro, Boroa Norte) B dorsal yellow pattern and b belly with yellow crosslinks (El Socorro) C dorsal pattern yellow with brown spots and c belly with yellow longitudinal spots (El Socorro, Boroa Norte) D dorsal pattern dark brown and d belly with whitish faded spots. All specimens were adults ranging in size from 4 to 5 cm.
Interspecific competition slows range expansion and shapes range boundaries
<p class="western"><span><span>Species expanding into new habitats as a result of climate change or human introductions will frequently encounter resident competitors. Theoretical models suggest that such interspecific competition can alter the speed of expansion and the shape of expanding range boundaries. However, competitive interactions are rarely considered when forecasting the success or speed of expansion, in part because there has been no direct experimental evidence that competition affects either expansion speed or boundary shape. Here we demonstrate that interspecific competition alters both expansion speed and range boundary shape. Using a two-species experimental system of the flour beetles <i>Tribolium castaneum</i> and <i>Tribolium</i> <i>confusum</i>, we show that interspecific competition dramatically slows expansion across a landscape over multiple generations. Using a parameterized stochastic model of expansion, we find that this slowdown can persist over the long-term. We also find that the shape of the moving range boundary changes continuously over many generations of expansion, first steepening and then becoming shallower, due to the competitive effect of the resident and density-dependent dispersal of the invader. This dynamic boundary shape suggests that current forecasting approaches assuming a constant shape could be misleading. More broadly, our results demonstrate that interactions between competing species can play a large role during range expansions and thus should be included in models and studies that monitor, forecast, or manage expansions in natural systems.</span></span></p>
Fig. 2 in INSUFFICIENT COLD RESISTANCE AND THE EASTERN BOUNDARY OF THE DISTRIBUTION RANGE OF ANT LASIUS FULIGINOSUS (HYMENOPTERA: FORMICIDAE)
Fig. 2 Dynamics of the minimal decade temperatures of 2018–2019 in the nest of the Lasius fuliginosus at the depth 20–30 cm (dotted line) and 50–60 cm (solid line) in vicinity
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Allen Brain Atlas
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Annotated Behaviour and Observability Dataset (ABODe)
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