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64 results for “extirpation”
Data from: Human-mediated extirpation of the unique Chatham Islands sea lion and implications for the conservation management of remaining New Zealand sea lion populations
While terrestrial megafaunal extinctions have been well characterized worldwide, our understanding of declines in marine megafauna remains limited. Here, we use ancient DNA analyses of prehistoric (<1450–1650 AD) sea lion specimens from New Zealand's isolated Chatham Islands to assess the demographic impacts of human settlement. These data suggest there was a large population of sea lions, unique to the Chatham Islands, at the time of Polynesian settlement. This distinct mitochondrial lineage became rapidly extinct within 200 years due to overhunting, paralleling the extirpation of a similarly large endemic mainland population. Whole mitogenomic analyses confirm substantial intraspecific diversity among prehistoric lineages. Demographic models suggest that even low harvest rates would likely have driven rapid extinction of these lineages. This study indicates that surviving Phocarctos populations are remnants of a once diverse and widespread sea lion assemblage, highlighting dramatic human impacts on endemic marine biodiversity. Our findings also suggest that Phocarctos bycatch in commercial fisheries may contribute to the ongoing population decline.
FIGURES 2–8 in Subfossils of extinct and extant species of Simuliidae (Diptera) from Austral and Cook Islands (Polynesia): anthropogenic extirpation of an aquatic insect?
FIGURES 2–8. Simulium (I.) teruamanga. Fig. 2. Dorsal view of head of extant larva. Matavera Stream, Rarotonga (scale bar 0.1 mm). Fig. 3. Hypostoma and postgenal cleft of extant larva (scale bar 0.05 mm). Fig. 4. Hypostoma of extant larva (scale bar 0.02 mm). Fig. 5. Hypostoma, postgenal cleft and genae of subfossil larva. Near outlet Tamarua East swamp, Mangaia (scale bar 0.1 mm). Fig. 6. Hypostoma of subfossil larva. Near outlet Tamarua East swamp, Mangaia (scale bar 0.02 mm). Fig. 7. Hypostoma, postgenal cleft, frontoclypeal apotome and antenna of subfossil larva. Near Lake Te Roto, Atiu (scale bar 0.1 mm). Fig. 8. Hypostoma of subfossil larva. Near Lake Te Roto, Atiu (scale bar 0.02 mm).
FIGURE 1 in Subfossils of extinct and extant species of Simuliidae (Diptera) from Austral and Cook Islands (Polynesia): anthropogenic extirpation of an aquatic insect?
FIGURE 1. Distribution of known simuliid material on Cook and Austral Islands. Simulium (I.) teruamanga—squares, S. (I.) rurutuense—circles. Simulium (I.) raivavaense—asterisk. Solid shapes indicates extant species, stippled subfossil material. (Adapted from Craig et al. 2001).
FIGURES 9–17. 9–13 in Subfossils of extinct and extant species of Simuliidae (Diptera) from Austral and Cook Islands (Polynesia): anthropogenic extirpation of an aquatic insect?
FIGURES 9–17. 9–13. Simulium (I.) rurutuense. Fig. 9. Dorsal view of head of extant larva. Vaipapa Stream, Rurutu (scale bar 0.1 mm). Fig. 10. Hypostoma and postgenal cleft of extant larva (scale bar 0.1 mm). Fig. 11. Hypostoma of extant larva (scale bar 0.02 mm). Fig. 12. Hypostoma, postgenal cleft and genae of subfossil larva. Mihiura Swamp, Tubuai (scale bar 0.1 mm). Fig. 13. Hypostoma of subfossil larva (scale bar 0.05 mm). 14–17. Simulium (I.) raivavaense. Near Rairua, Raivavae. Fig. 14. Frontoclypeal apotome of extinct subfossil larva—note anteromedial palatal brush (scale bar 0.05 mm). Fig.15. Hypostoma, postgenal cleft and genae of extinct subfossil larva (scale bar 0.05 mm). Fig. 16. Hypostoma of last instar of extinct subfossil larva (scale bar 0.02 mm). Fig. 17. Hypostoma of probable penultimate instar of larva (scale bar 0.02 mm).
Distribution. Most of Africa S of the Sahara Desert, except in lowland tropical rainforests. Spotted Hyenas have been extirpated from many areas of southern Africa. in Hyaenidae
Distribution. Most of Africa S of the Sahara Desert, except in lowland tropical rainforests. Spotted Hyenas have been extirpated from many areas of southern Africa.
Subspecies and Distribution. U. a. arctos Linnaeus, 1758 — Europe and W Russia. U. a. alascensis Merriam, 1896 — most of Alaska (excluding Alaska Peninsula, SE panhandle & Kodiak Island group). U. a. beringianus Middendorff, 1853 — NE Russia (Kamchatka Peninsula & N Kuril Islands northward through the Koryak Autonomous District, and along W coast of the Sea of Okhotsk). U. a. collaris Cuvier, 1824 — Russia (Siberia, from E of the Yenisey River to the Bering Sea, but excluding Kamchatka and more southern parts of the Russian Far East), N Mongolia. U. a. dalli Merriam, 1896 — SE Alaska (N of Alexander Archipelago). U. a. gyas Merriam, 1902 — Alaska peninsula. U. a. horribilis Ord, 1815 —W Canada (Yukon, North-West Territories, British Columbia & Alberta), inland W USA (extirpated from S Wyoming to Mexico). U. a. isabellinus Horsfield, 1826 — N India, Pakistan, Afghanistan, N to Kazakhstan and Mongolia (Gobi Desert). U. a. lasiotus Gray, 1867 — Russia (Southern Kuril Islands, Sakhalin, Ussuri/Amur river region of the Russian Far East), NE China, North Korea, and Japan (Hokkaido). U. a. middendorffi Merriam, 1896 — Alaska (Kodiak Island & nearby islands). U. a. pruinosus Blyth, 1853 — Tibetan Plateau, China, N Nepal. U. a. sitkensis Merriam, 1896 — SE Alaska (Alexander Archipelago & adjacent coastal area). U. a. stikeenensis Merriam, 1914 — W Canada (W British Columbia), and formerly W USA (W Washington and Oregon). U. a. syriacus Hemprich & Ehrenberg, 1828 — Middle East, from Turkey to Iran (extirpated in Syria), Caucasus mountains of Russia, Georgia, Armenia and Azerbaijan. in Ursidae
Subspecies and Distribution. U. a. arctos Linnaeus, 1758 — Europe and W Russia. U. a. alascensis Merriam, 1896 — most of Alaska (excluding Alaska Peninsula, SE panhandle & Kodiak Island group). U. a. beringianus Middendorff, 1853 — NE Russia (Kamchatka Peninsula & N Kuril Islands northward through the Koryak Autonomous District, and along W coast of the Sea of Okhotsk). U. a. collaris Cuvier, 1824 — Russia (Siberia, from E of the Yenisey River to the Bering Sea, but excluding Kamchatka and more southern parts of the Russian Far East), N Mongolia. U. a. dalli Merriam, 1896 — SE Alaska (N of Alexander Archipelago). U. a. gyas Merriam, 1902 — Alaska peninsula. U. a. horribilis Ord, 1815 —W Canada (Yukon, North-West Territories, British Columbia & Alberta), inland W USA (extirpated from S Wyoming to Mexico). U. a. isabellinus Horsfield, 1826 — N India, Pakistan, Afghanistan, N to Kazakhstan and Mongolia (Gobi Desert). U. a. lasiotus Gray, 1867 — Russia (Southern Kuril Islands, Sakhalin, Ussuri/Amur river region of the Russian Far East), NE China, North Korea, and Japan (Hokkaido). U. a. middendorffi Merriam, 1896 — Alaska (Kodiak Island & nearby islands). U. a. pruinosus Blyth, 1853 — Tibetan Plateau, China, N Nepal. U. a. sitkensis Merriam, 1896 — SE Alaska (Alexander Archipelago & adjacent coastal area). U. a. stikeenensis Merriam, 1914 — W Canada (W British Columbia), and formerly W USA (W Washington and Oregon). U. a. syriacus Hemprich & Ehrenberg, 1828 — Middle East, from Turkey to Iran (extirpated in Syria), Caucasus mountains of Russia, Georgia, Armenia and Azerbaijan.
Distribution. NE & SE Pakistan, India, S Nepal, Bangladesh, where it has been almost extirpated, and Sri Lanka. Doubtful records from Myanmar and China (Yunnan). in Manidae
Distribution. NE & SE Pakistan, India, S Nepal, Bangladesh, where it has been almost extirpated, and Sri Lanka. Doubtful records from Myanmar and China (Yunnan).
Distribution. NE Pakistan, lowland areas of S Nepal, and Peninsular India. Introduced into Italy near Rome (extirpated during World War II), South Africa, S USA (Texas), and N Mexico (Coahuila, Nuevo Leon, Sonora, Tamaulipas & Veracruz). in Bovidae
Distribution. NE Pakistan, lowland areas of S Nepal, and Peninsular India. Introduced into Italy near Rome (extirpated during World War II), South Africa, S USA (Texas), and N Mexico (Coahuila, Nuevo Leon, Sonora, Tamaulipas & Veracruz).
Data from: Reintroducing extirpated herbivores could partially reverse the late Quaternary decline of large and grazing species
<p><strong>Aim: </strong>Reinstating large, native herbivores is an essential component of ecological restoration efforts, as these taxa can be important drivers of ecological processes. However, many herbivore species have gone globally or regionally extinct during the last 50,000 years, leaving simplified herbivore assemblages and trophically downgraded ecosystems. Here, we discuss to what extent trophic rewilding can undo these changes by reinstating native herbivores.</p> <p><strong>Location: </strong>Global</p> <p><strong>Time Period: </strong>We report functional trait changes from the Late Pleistocene to the present, and estimated trait changes under future scenarios.</p> <p><strong>Major Taxa Studied: </strong>Wild, large (≥10 kg), terrestrial, mammalian herbivores</p> <p><strong>Methods: </strong>We use a functional trait dataset containing all late Quaternary large herbivores ≥10 kg to look at changes in the body mass and diet composition of herbivore assemblages, a proxy for species' ecological effects. First, we assess how these traits have changed from the Late Pleistocene to the present. Next, we quantify how the current body mass and diet composition would change if all extant, wild herbivores were restored to their native ranges (and if no functional replacements were used), exploring scenarios with different baselines.</p> <p><strong>Results: </strong>Defaunation has primarily removed large and grazing herbivores. Reinstating extant herbivores across their native ranges would reverse these changes, especially when reinstating them to their prehistoric distributions. It would partially restore herbivore body mass and diet composition to pre-anthropogenic conditions. However, in the absence of complementary interventions (e.g. introducing functional replacements), many herbivore assemblages would remain down-sized and browser dominated, relative to pre-anthropogenic conditions.</p> <p><strong>Main Conclusions: </strong>Many terrestrial herbivore assemblages - and hence ecosystems - would remain trophically downgraded, even after bringing back all extant, native herbivores. Therefore, complementary interventions would be required to achieve complete functional restoration. Nevertheless, our findings suggest that reintroducing the remaining native herbivores would diversify the herbivory and disturbances of herbivore assemblages.</p>
Distribution. Most of Africa S of the Sahara Desert, except in lowland tropical rainforests. Spotted Hyenas have been extirpated from many areas of southern Africa. in Hyaenidae
Distribution. Most of Africa S of the Sahara Desert, except in lowland tropical rainforests. Spotted Hyenas have been extirpated from many areas of southern Africa.
Distribution. NE Pakistan, lowland areas of S Nepal, and Peninsular India. Introduced into Italy near Rome (extirpated during World War II), South Africa, S USA (Texas), and N Mexico (Coahuila, Nuevo Leon, Sonora, Tamaulipas & Veracruz). in Bovidae
Distribution. NE Pakistan, lowland areas of S Nepal, and Peninsular India. Introduced into Italy near Rome (extirpated during World War II), South Africa, S USA (Texas), and N Mexico (Coahuila, Nuevo Leon, Sonora, Tamaulipas & Veracruz).
Distribution. From Colombia and Venezuela to S Brazil, Paraguay, and N Argentina; it also occurs on Trinidad I, and previously was found on Tobago I, but has been extirpated from there recently. in Cervidae
Distribution. From Colombia and Venezuela to S Brazil, Paraguay, and N Argentina; it also occurs on Trinidad I, and previously was found on Tobago I, but has been extirpated from there recently.
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.
Distribution. Patchily in forests not more than 350 km inland from the coast in S Nigeria (W limit in forests near Dahomey Gap), W Cameroon, W Equatorial Guinea, W Gabon, and SW of the Republic of Congo (as far S as Conkouati-Douli National Park); there have been unconfirmed reports of its occurrence in Benin, butif it ever did occur there, it may now be extirpated, as was a former population near the Benue River in Nigeria. in Cercopithecidae
Distribution. Patchily in forests not more than 350 km inland from the coast in S Nigeria (W limit in forests near Dahomey Gap), W Cameroon, W Equatorial Guinea, W Gabon, and SW of the Republic of Congo (as far S as Conkouati-Douli National Park); there have been unconfirmed reports of its occurrence in Benin, butif it ever did occur there, it may now be extirpated, as was a former population near the Benue River in Nigeria.
Distribution. Known only from scattered localities on Peninsular Malaysia; it may be extirpated in most ofits historical distribution in SE Myanmar (Bago Division and Mon State) and W & Peninsular Thailand. in Muridae
Distribution. Known only from scattered localities on Peninsular Malaysia; it may be extirpated in most ofits historical distribution in SE Myanmar (Bago Division and Mon State) and W & Peninsular Thailand.
Figure 9 in Spatial and temporal distributions of juvenile horseshoe crabs (Arthropoda: Chelicerata) approaching extirpation along the northwestern shoreline of the New Territories of Hong Kong SAR, China
Figure 9. Frequency distributions of distances from (A) the nearest sea grass beds and (B) the nearest oyster beds where juvenile Tachypleus tridentatus individuals were obtained in the study area.
Figure 7 in Spatial and temporal distributions of juvenile horseshoe crabs (Arthropoda: Chelicerata) approaching extirpation along the northwestern shoreline of the New Territories of Hong Kong SAR, China
Figure 7. Temporal variations in the distribution of juvenile Tachypleus tridentatus individuals downshore from the shoreline at Stations E, F and H with means and standard deviations also shown.
Figure 8 in Spatial and temporal distributions of juvenile horseshoe crabs (Arthropoda: Chelicerata) approaching extirpation along the northwestern shoreline of the New Territories of Hong Kong SAR, China
Figure 8. Frequency distributions of (A) sediment temperature, (B) salinity and (C) dissolved oxygen concentration of interstitial waters where juvenile Tachypleus tridentatus individuals were obtained in the study area.
Figure 5 in Spatial and temporal distributions of juvenile horseshoe crabs (Arthropoda: Chelicerata) approaching extirpation along the northwestern shoreline of the New Territories of Hong Kong SAR, China
Figure 5. The spatial distribution of juvenile Tachypleus tridentatus individuals of different prosomal width ranges at Stations E, F and H.
Figure 6 in Spatial and temporal distributions of juvenile horseshoe crabs (Arthropoda: Chelicerata) approaching extirpation along the northwestern shoreline of the New Territories of Hong Kong SAR, China
Figure 6. Temporal variations in the total abundance of juvenile Tachypleus tridentatus individuals at Stations E (Ɨ), F (-) and H (Δ).
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