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Data from: The population origins and expansion of feral cats in Australia
The historical literature suggests that in Australia, the domestic cat (Felis catus) had a European origin [~200 years before present (ybp)], but it is unclear if cats arrived from across the Asian land bridge contemporaneously with the dingo (4000 ybp), or perhaps immigrated ~40000 ybp in association with Aboriginal settlement from Asia. The origin of cats in Australia is important because the continent has a complex and ancient faunal assemblage that is dominated by endemic rodents and marsupials and lacks the large placental carnivores found on other large continents. Cats are now ubiquitous across the entire Australian continent and have been implicit in the range contraction or extinction of its small to medium sized (<3.5kg) mammals. We analyzed the population structure of 830 cats using 15 short tandem repeat (STR) genomic markers. Their origin appears to come exclusively from European founders. Feral cats in continental Australia exhibit high genetic diversity in comparison with the low diversity found in populations of feral cats living on islands. The genetic structure is consistent with a rapid westerly expansion from eastern Australia and a limited expansion in coastal Western Australia. Australian cats show modest if any population structure and a close genetic alignment with European feral cats as compared to cats from Asia, the Christmas and Cocos (Keeling) Islands (Indian Ocean), and European wildcats (F. silvestris silvestris).
Data from: Effects of feral cats on the evolution of anti-predator behaviours in island reptiles: insights from an ancient introduction
Exotic predators have been the driving force behind the extinction of many island endemic species. We examined impacts of feral cats (Felis catus) on the abundance and anti-predator behaviors of Aegean wall lizards (Podarcis erhardii) in the Cyclades (Greece), where cats were introduced thousands of years ago. We compared populations with high and low cat density on Naxos and populations on surrounding islets with no cats. Results show that cats have strong negative effects on wall lizard populations, and lizards cope with current threat from cats using plastic defenses that likely existed before the ancient introduction. Lizards facing greater risk from cats stayed closer to refugia, and were more likely to shed their tails in a standardized assay. Flight initiation distance from a surveyor or a mounted cat decoy in the lab correlated closely with risk from cats. All populations showed phenotypic plasticity in flight initiation distance suggesting that this plasticity is ancient and could have helped wall lizards survive the initial introduction of cats to the region. Lizards from islets sought shelter less often and often initially approached the cat decoy. These differences reflect a change since the introduction and could render islet lizards strongly susceptible to cat predation.
Data from: Estimating feral cat densities using distance sampling in an urban environment
1. Estimating feral cat population densities in urban environments can be difficult due to lack of public space and human interference. The purpose of this study was to use distance sampling in a citywide landscape to determine population size and areas of high abundance to inform trap-neuter-release management programs. 2. Line transect distance sampling was used to estimate density of the feral cat population in Windsor, Ontario from June to July 2014. Windsor has a human population of 217,188 and is about 146 km2 in size. Most transects were placed along local roads. 3. Density was estimated at about 13.3 (95% CI 9.7 – 18.1) cats per km2, and an estimated population size of 1858 cats (95% CI 1361 – 2537) with the highest relative density occurring in West and Central Windsor. 4. Urban wildlife managers could utilize these methods to monitor feral cat populations and evaluate the effectiveness of trap-neuter-release programs.
Data from: Experimental exposure to trace metals affects plumage bacterial community in the feral pigeon
Bacteria are fundamental associates of animals, and recent studies have highlighted their major role in host behaviour, immunity or reproductive investment. Thus, any environmental factor modifying bacterial community may affect host fitness. In birds, trace metals emitted by anthropogenic activities accumulate onto the plumage where they may alter bacterial community and ultimately affect bird fitness. Although trace metals are current major environmental issues in urban habitats, their effects on feather bacterial community have never been investigated. Here, we supplemented feral pigeons Columba livia, an emblematic urban species, with zinc and/or lead in drinking and bath water. As expected, lead and zinc supplementations modified plumage bacterial community composition. Zinc decreased bacterial load, while lead decreased bacterial richness and the frequency of preening behaviour in birds, known to regulate feather bacteria. Our results demonstrate for the first time the effects of common urban trace metals on plumage bacterial community and shed light on one of the mechanisms by which trace metals can affect bird fitness. Further studies are now needed to investigate how this effect modulates avian life history traits known to depend on plumage bacterial community.
Data from: Genetic diversity of oilseed rape fields and feral populations in the context of coexistence with GM crops
Despite growing concern about transgenes escaping from fields, few studies have analysed the genetic diversity of crops in an agroecosystem over several years. Accurate information about the dynamics and relationship of the genetic diversity of crops in an agroecosystem is essential for risk assessment and policies concerning the containment of genetically modified crops and their coexistence with crops grown by conventional practices. Here, we analysed the genetic diversity of oilseed rape plants from fields and feral populations over 4 years in an agricultural landscape of 41 km2. We used exact compatibility and maximum likelihood assignment methods to assign these plants to cultivars. Even pure lines and hybrid cultivar seed lots contained several genotypes. The cultivar diversity in fields reflected the conventional view of agroecosystems quite well: that is, there was a succession of cultivars, some grown for longer than others because of their good performance, some used for one year and then abandoned, and others gradually adopted. Three types of field emerged: fields sown with a single cultivar, fields sown with two cultivars, and unassigned fields (too many cultivars or unassigned plants to reliably assign the field). Field plant diversity was higher than expected, indicating the persistence of cultivars that were grown for only one year. The cultivar composition of feral populations was similar to that of field plants, with an increasing number of cultivars each year. By using genetic tools, we found a link between the cultivars of field plants in a particular year and the cultivars of feral population plants in the following year. Feral populations on road verges were more diverse than those on path verges. All of these findings are discussed in terms of their consequences in the context of coexistence with genetically modified crops.
Data from: On the occurrence of three non-native cichlid species including the first record of a feral population of Pelmatolapia (Tilapia) mariae (Boulenger, 1899) in Europe
Thermally influenced freshwater systems provide suitable conditions for non-native species of tropical and subtropical origin to survive and form proliferating populations beyond their native ranges. In Germany, non-native convict cichlids (Amatitlania nigrofasciata) and tilapia (Oreochromis sp.) have established populations in the Gillbach, a small stream that receives warm water discharge from a local power plant. Here, we report on the discovery of spotted tilapia (Pelmatolapia mariae) in the Gillbach, the first record of a reproducing population of this species in Europe. It has been hypothesized that Oreochromis sp. in the Gillbach are descendants of aquaculture escapees and our mtDNA analysis found both O. mossambicus and O. niloticus maternal lineages, which are commonly used for hybrids in aquaculture. Convict cichlids and spotted tilapia were most probably introduced into the Gillbach by aquarium hobbyists. Despite their high invasiveness worldwide, we argue that all three cichlid species are unlikely to spread and persist permanently beyond the thermally influenced range of the Gillbach river system. However, convict cichlids from the Gillbach are known to host both native and non-native fish parasites and thus, non-native cichlids may constitute threats to the native fish fauna. We therefore strongly recommend continuous monitoring of the Gillbach and similar systems.
Data from: Crossed effects of helminth infection and lead exposure on fitness: an experimental study in feral pigeons (Columba livia)
<p><span>Living organisms are exposed to multiple environmental factors that can affect their fitness. The effects of these simultaneous stressors can be additive or can interact in negative synergistic or antagonistic ways to affect the health of exposed individuals. Parasites can accumulate pollutants in their own tissues and have been shown to increase the tolerance of their hosts to different pollutants (antagonistic interaction between parasites and pollutants). We tested the existence of combined antagonistic effects between intestinal parasites and lead exposure on urban feral pigeons (<em>Columba livia</em>) which are known to be exposed to trace metal pollution and harbor a wide variety of internal and external parasites. </span><span>We experimentally exposed feral pigeons to two treatments: an anthelmintic treatment to eliminate intestinal nematode parasites; an exposure to lead for a period of 6 months. We tested the effects of these crossed treatments on several components of fitness: immunocompetence, reproduction, and body mass. </span><span>Our findings suggest that the overall effects of lead exposure, either alone or in combination with the presence of intestinal parasites (without </span><span>anthelmintic </span><span>treatment) were negative, through either additive or synergistic means. </span><span>In the absence of putative antagonistic effects between lead exposure and with helminths, the detoxification hypothesis could not be confirmed. </span><span>Our results reveal the existence of negative combined effects between pollutant exposure and intestinal parasites, highlighting the importance of accounting for multiple stress factors when studying the effects of exposure to pollutants and/or other environmental stressors on the fitness of organisms.</span></p>
Subspecies and Distribution. B. j. javanicus d'Alton, 1823 — Java, perhaps Bali. B. j. birmanicus Lydekker, 1898 — Asian mainland including Myanmar, S China (S Yunnan, current presence uncertain), Laos, Vietnam, Thailand, Cambodia, and N Peninsular Malaysia. B. j. low: Lydekker, 1912 — Borneo. The domestic form of the Banteng has been introduced, and is now feral, in N Australia, New Guinea, and on various islands of Indonesia (Bali, Sangihe, Sulawesi, Sumbawa, Sumba, and Enggano) and occurs in domestication throughout the islands of SE Asia. in Bovidae
Subspecies and Distribution. B. j. javanicus d'Alton, 1823 — Java, perhaps Bali. B. j. birmanicus Lydekker, 1898 — Asian mainland including Myanmar, S China (S Yunnan, current presence uncertain), Laos, Vietnam, Thailand, Cambodia, and N Peninsular Malaysia. B. j. low: Lydekker, 1912 — Borneo. The domestic form of the Banteng has been introduced, and is now feral, in N Australia, New Guinea, and on various islands of Indonesia (Bali, Sangihe, Sulawesi, Sumbawa, Sumba, and Enggano) and occurs in domestication throughout the islands of SE Asia.
Subspecies and Distribution. S. s. scrofa Linnaeus, 1758 — W Europe, from Denmark, Germany, Poland, and Czech Republic to N Italy and N Iberian Peninsula; possibly also Albania. The taxonomic status of animals in Austria, Switzerland, Slovenia, and Slovakia is unclear but presumably these populations are included in scrofa, as are the populations of Sweden, Finland, and the Baltic states. However, restocking of once depleted populations, for example in Italy, has likely involved the introduction and mixing of this subspecies with other subspecies, such as attila. S. s. affinis Gray, 1847 — S India and Sri Lanka. S. s. algirus Loche, 1867 — Tunisia, Algeria, and Morocco, on the coastal side of the mountains or in the low montane areas. S. s. attila Thomas, 1912 — Hungary, Ukraine, C & S Belarus, Romania, Moldova, and S Russia towards the N flank of the Caucasus, but not including the Transcaucasian countries of Georgia, Armenia, and Azerbaijan. The range possibly extends as far S as the Mesopotamian Delta in Iraq, in which case it would likely include W & SW Iran, and possibly E Turkey and Syria, where it borders with lybicus. Such a range could not be easily reconciled with a statement by Groves that "the difference between pigs from N and S of the Caucasus is quite striking; Transcaucasian boars are certainly not attila." This subspecies may also extend into C Asia and include Kazakhstan, Uzbekistan, and Turkmenistan, but no data exist to support this. S. s. baeticus Thomas, 1912 — originally described from Coto Donana, S Spain, and later merged with meridionalis; also S Portugal. Unless evidence is found that these Italian and Iberian populations are the relics of a much larger formerly contiguous range, this subspecies should be kept as distinct. S. s. coreanus Heude, 1897 — Korean Peninsula. S. s. eristatus Wagner, 1839 — Himalayas S to C India and E to Indochina (N of the Kra Isthmus). S. s. davidi Groves, 1981 — the arid zone from E Iran to Gujarat, including Pakistan and NW India, and perhaps N to Tajikistan. S. s. leucomystax Temminck, 1842 — main Is ofJapan (Honshu, Shikoku, Kyushu, Nakadori, Hiburijima, Tojima, Kushima, and other smaller Is). S. s. lybicus Gray, 1868 — Bulgaria, Greece, Turkey, Syria, Jordan, Israel, Palestine, in the past also in Lybia, and Egypt. The former Yugoslavia was included in its range, which would suggest that now Slovenia, Serbia, Croatia, Bosnia and Herzegovina, Montenegro, and Kosovo are within the range of this subspecies, although the exact boundaries are unclear. Pigs from Albania have been assigned to S. s. scrofa. S. s. majori De Beaux & Festa, 1927 — C & S Italian Peninsula. S. s. menidionalis Forsyth Major, 1882 — Corsica and Sardinia, with the proviso that the two populations are very likely to be introduced or feral. S. s. moupinensis Milne-Edwards, 1871 — China, S to Vietnam and W to Sichuan. S. s. nigripes Blanford, 1875 — the flanks of the Tianshan mountains in Kyrgyzstan and NW China (Xinjiang). An animal photographed in NE Iran (Golestan) looked like this subspecies. S. s. nukiuanus Kuroda, 1924 — Iriomote, Ishigaki, Okinawa, Tokunoshima, Amamioshima, and Kakerome Is in the Ryukyu chain in extreme S Japan, though some of these populations have hybridized with introduced domesticates. S. s. sibiricus Staffe, 1922 — Mongolia and Transbaikal (S & E of Lake Baikal). S. s. tawvanus Swinhoe, 1863 — Taiwan. S. s. ussuricus Heude, 1888 — far E Russia and the Manchurian region (China). Korean populations were previously included in this subspecies, but based on new evidence, the Korean taxon seems more similar to moupinensis. S. s. vittatus Boie, 1828 — Malay Peninsula, S of the Isthmus of Kra, the offshore islands of Terutai and Langkawi, Sumatra, Riau Archipelago, Java, Bali, and a range of smaller islands around these, including Babi, Bakong, Batam, Bawean, Bengkalis, Bintan, Bulan, Bunguran, Cuyo, Deli, Durian, Enggano, Galang, Jambongan, Karimon (Riau Is), Kundur, Lagong, Laut, Lingga, Lingung, Mapor, Moro Kecil, North Pagai, Nias, Panaitan, Payong, Penang, Pinie, Rupat, Siantan, Siberut, Simeulue, Singkep, Sugi, Sugi Bawa, Telibon, Tinggi, Tuangku, and the Tambelan Is. This species was originally present from the British Is in the extreme W, through Eurasia from S Scandinavia to S Siberia, extending as far E as Korea and Japan, and SE into some of the Sunda Is and Taiwan. In the S the species ranged along the Nile Valley to Khartoum, and N of the Sahara in Africa, more orless following the continental coasts of S, E, and SE Asia. Within this range it was absent only from extremely dry deserts, e.g. the driest regions of Mongolia and in China W of Sichuan; and alpine zones, such as the high altitudes of Pamir and Tien Shan. In recent centuries, the range of S. scrofa has changed dramatically because of hunting and changes in available habitat. The species disappeared from the British Is in the 17" century, from Denmark in the 19" century, and was greatly reduced in range and numbers in the 20" century from areas as distant as Tunisia, Sudan, Germany, and Russia. Following these severe declines, there were some slight population recoveries in Russia, Italy, Spain, and Germany in the mid-20™ century, and natural and assisted range expansions in Denmark and Sweden. The species has also been inadvertently reintroduced in various locations in the Great Britain via escapees of mixed origin from commercial farming enterprises. Ex-S. scrofa stocks also occur as introduced feral populations in various other parts of the world, including Australia, New Zealand, the eastern Malay Archipelago, and in North, Central, and South America. In all of these areas they are now generally recognized as a major pest. in Suidae
Subspecies and Distribution. S. s. scrofa Linnaeus, 1758 — W Europe, from Denmark, Germany, Poland, and Czech Republic to N Italy and N Iberian Peninsula; possibly also Albania. The taxonomic status of animals in Austria, Switzerland, Slovenia, and Slovakia is unclear but presumably these populations are included in scrofa, as are the populations of Sweden, Finland, and the Baltic states. However, restocking of once depleted populations, for example in Italy, has likely involved the introduction and mixing of this subspecies with other subspecies, such as attila. S. s. affinis Gray, 1847 — S India and Sri Lanka. S. s. algirus Loche, 1867 — Tunisia, Algeria, and Morocco, on the coastal side of the mountains or in the low montane areas. S. s. attila Thomas, 1912 — Hungary, Ukraine, C & S Belarus, Romania, Moldova, and S Russia towards the N flank of the Caucasus, but not including the Transcaucasian countries of Georgia, Armenia, and Azerbaijan. The range possibly extends as far S as the Mesopotamian Delta in Iraq, in which case it would likely include W & SW Iran, and possibly E Turkey and Syria, where it borders with lybicus. Such a range could not be easily reconciled with a statement by Groves that "the difference between pigs from N and S of the Caucasus is quite striking; Transcaucasian boars are certainly not attila." This subspecies may also extend into C Asia and include Kazakhstan, Uzbekistan, and Turkmenistan, but no data exist to support this. S. s. baeticus Thomas, 1912 — originally described from Coto Donana, S Spain, and later merged with meridionalis; also S Portugal. Unless evidence is found that these Italian and Iberian populations are the relics of a much larger formerly contiguous range, this subspecies should be kept as distinct. S. s. coreanus Heude, 1897 — Korean Peninsula. S. s. eristatus Wagner, 1839 — Himalayas S to C India and E to Indochina (N of the Kra Isthmus). S. s. davidi Groves, 1981 — the arid zone from E Iran to Gujarat, including Pakistan and NW India, and perhaps N to Tajikistan. S. s. leucomystax Temminck, 1842 — main Is ofJapan (Honshu, Shikoku, Kyushu, Nakadori, Hiburijima, Tojima, Kushima, and other smaller Is). S. s. lybicus Gray, 1868 — Bulgaria, Greece, Turkey, Syria, Jordan, Israel, Palestine, in the past also in Lybia, and Egypt. The former Yugoslavia was included in its range, which would suggest that now Slovenia, Serbia, Croatia, Bosnia and Herzegovina, Montenegro, and Kosovo are within the range of this subspecies, although the exact boundaries are unclear. Pigs from Albania have been assigned to S. s. scrofa. S. s. majori De Beaux & Festa, 1927 — C & S Italian Peninsula. S. s. menidionalis Forsyth Major, 1882 — Corsica and Sardinia, with the proviso that the two populations are very likely to be introduced or feral. S. s. moupinensis Milne-Edwards, 1871 — China, S to Vietnam and W to Sichuan. S. s. nigripes Blanford, 1875 — the flanks of the Tianshan mountains in Kyrgyzstan and NW China (Xinjiang). An animal photographed in NE Iran (Golestan) looked like this subspecies. S. s. nukiuanus Kuroda, 1924 — Iriomote, Ishigaki, Okinawa, Tokunoshima, Amamioshima, and Kakerome Is in the Ryukyu chain in extreme S Japan, though some of these populations have hybridized with introduced domesticates. S. s. sibiricus Staffe, 1922 — Mongolia and Transbaikal (S & E of Lake Baikal). S. s. tawvanus Swinhoe, 1863 — Taiwan. S. s. ussuricus Heude, 1888 — far E Russia and the Manchurian region (China). Korean populations were previously included in this subspecies, but based on new evidence, the Korean taxon seems more similar to moupinensis. S. s. vittatus Boie, 1828 — Malay Peninsula, S of the Isthmus of Kra, the offshore islands of Terutai and Langkawi, Sumatra, Riau Archipelago, Java, Bali, and a range of smaller islands around these, including Babi, Bakong, Batam, Bawean, Bengkalis, Bintan, Bulan, Bunguran, Cuyo, Deli, Durian, Enggano, Galang, Jambongan, Karimon (Riau Is), Kundur, Lagong, Laut, Lingga, Lingung, Mapor, Moro Kecil, North Pagai, Nias, Panaitan, Payong, Penang, Pinie, Rupat, Siantan, Siberut, Simeulue, Singkep, Sugi, Sugi Bawa, Telibon, Tinggi, Tuangku, and the Tambelan Is. This species was originally present from the British Is in the extreme W, through Eurasia from S Scandinavia to S Siberia, extending as far E as Korea and Japan, and SE into some of the Sunda Is and Taiwan. In the S the species ranged along the Nile Valley to Khartoum, and N of the Sahara in Africa, more orless following the continental coasts of S, E, and SE Asia. Within this range it was absent only from extremely dry deserts, e.g. the driest regions of Mongolia and in China W of Sichuan; and alpine zones, such as the high altitudes of Pamir and Tien Shan. In recent centuries, the range of S. scrofa has changed dramatically because of hunting and changes in available habitat. The species disappeared from the British Is in the 17" century, from Denmark in the 19" century, and was greatly reduced in range and numbers in the 20" century from areas as distant as Tunisia, Sudan, Germany, and Russia. Following these severe declines, there were some slight population recoveries in Russia, Italy, Spain, and Germany in the mid-20™ century, and natural and assisted range expansions in Denmark and Sweden. The species has also been inadvertently reintroduced in various locations in the Great Britain via escapees of mixed origin from commercial farming enterprises. Ex-S. scrofa stocks also occur as introduced feral populations in various other parts of the world, including Australia, New Zealand, the eastern Malay Archipelago, and in North, Central, and South America. In all of these areas they are now generally recognized as a major pest.
Subspecies and Distribution. B.j.javanicusd'Alton,1823—Java,perhapsBali. B.j.birmanicusLydekker,1898—AsianmainlandincludingMyanmar,SChina(SYunnan,currentpresenceuncertain),Laos,Vietnam,Thailand,Cambodia,andNPeninsularMalaysia. B. j. low: Lydekker, 1912 — Borneo. The domestic form of the Banteng has been introduced, and is now feral, in N Australia, New Guinea, and on various islands of Indonesia (Bali, Sangihe, Sulawesi, Sumbawa, Sumba, and Enggano) and occurs in domestication throughout the islands of SE Asia. in Bovidae
Subspecies and Distribution. B.j.javanicusd'Alton,1823—Java,perhapsBali. B.j.birmanicusLydekker,1898—AsianmainlandincludingMyanmar,SChina(SYunnan,currentpresenceuncertain),Laos,Vietnam,Thailand,Cambodia,andNPeninsularMalaysia. B. j. low: Lydekker, 1912 — Borneo. The domestic form of the Banteng has been introduced, and is now feral, in N Australia, New Guinea, and on various islands of Indonesia (Bali, Sangihe, Sulawesi, Sumbawa, Sumba, and Enggano) and occurs in domestication throughout the islands of SE Asia.
Subspecies and Distribution. R.t.tarandusLinnaeus,1758—Norway. R.t.caribouGmelin,1788—SCanada(fromSYukontoLabradorandNewfoundland)andNWUSA(NEWashington,NIdaho&WMontana). R.t.fennicusLonnberg,1909—FinlandandNWRussia(Karelia). R.t.groenlandicusLinnaeus,1767—Alaska,NCanada,WGreenland. R.t.pearsoniLydekker,1903—NovayaZemlya(Russia). R.t.pearyiJ.A.Allen,1902—CanadianArcticIs. R. t. phylarchus Hollister, 1912 — Russian Far East (Amur region, Okhotsk area, Sakhalin, Kamchatka). R.t.platyrhynchusVrolik,1829—Svalbard(Norway). R.t.sibiricusMurray,1866—NSiberiantundra,RussianArcticIs. R. t. valentinae Flerov, 1933 — Ural Mts (Russia), Altai Mts, Mongolia. Feral Icelandic population originated from animals introduced from Norway in 1771; they have been introduced also into South Georgia Is (in 1911-1912 and 1925) and Kerguelen Is (in 1955). in Cervidae
Subspecies and Distribution. R.t.tarandusLinnaeus,1758—Norway. R.t.caribouGmelin,1788—SCanada(fromSYukontoLabradorandNewfoundland)andNWUSA(NEWashington,NIdaho&WMontana). R.t.fennicusLonnberg,1909—FinlandandNWRussia(Karelia). R.t.groenlandicusLinnaeus,1767—Alaska,NCanada,WGreenland. R.t.pearsoniLydekker,1903—NovayaZemlya(Russia). R.t.pearyiJ.A.Allen,1902—CanadianArcticIs. R. t. phylarchus Hollister, 1912 — Russian Far East (Amur region, Okhotsk area, Sakhalin, Kamchatka). R.t.platyrhynchusVrolik,1829—Svalbard(Norway). R.t.sibiricusMurray,1866—NSiberiantundra,RussianArcticIs. R. t. valentinae Flerov, 1933 — Ural Mts (Russia), Altai Mts, Mongolia. Feral Icelandic population originated from animals introduced from Norway in 1771; they have been introduced also into South Georgia Is (in 1911-1912 and 1925) and Kerguelen Is (in 1955).
Subspecies and Distribution. C.o.olivaceusSchomburgk,1848—mightberestrictedtotheVenezuelanAmazonBasinfromtheupperRioOrinoco,andthroughouttheOrinocosavannaabovethemouthoftheRioMeta,asfarNandWastheSierradePerijaandtheVenezuelanC.o.dela C.o. (C.o. Range), to the left bank of the Rio Essequibo in W Guyana, in forests of the Guiana Shield; distributional limits separating the two subspecies are not well known. C. o. castaneus 1. Geoffroy Saint-Hilaire, 1851 — Guianas (possibly from the Rio Essequibo in Guyana E through Suriname and French Guiana) and N Brazil, where its distributional limits are not well known but are possibly marked by the rios Negro and Branco and Catrimani (right bank affluent of the Rio Branco) in the W, the Rio Amazonas in the S, and the Atlantic coast in the E, and it also occurs on Caviana and Mexiana Is in the estuary of the Rio Amazonas. Small numbers introduced as pets are now feral on Margarita I off the Venezuelan coast. in Cebidae
Subspecies and Distribution. C.o.olivaceusSchomburgk,1848—mightberestrictedtotheVenezuelanAmazonBasinfromtheupperRioOrinoco,andthroughouttheOrinocosavannaabovethemouthoftheRioMeta,asfarNandWastheSierradePerijaandtheVenezuelanC.o.dela C.o. (C.o. Range), to the left bank of the Rio Essequibo in W Guyana, in forests of the Guiana Shield; distributional limits separating the two subspecies are not well known. C. o. castaneus 1. Geoffroy Saint-Hilaire, 1851 — Guianas (possibly from the Rio Essequibo in Guyana E through Suriname and French Guiana) and N Brazil, where its distributional limits are not well known but are possibly marked by the rios Negro and Branco and Catrimani (right bank affluent of the Rio Branco) in the W, the Rio Amazonas in the S, and the Atlantic coast in the E, and it also occurs on Caviana and Mexiana Is in the estuary of the Rio Amazonas. Small numbers introduced as pets are now feral on Margarita I off the Venezuelan coast.
Variant Call File (VCF) for Genome-wide polymorphism and genic selection in feral and domesticated lineages of Cannabis sativa
<p>A comprehensive understanding of the degree to which genomic variation is maintained by selection versus drift and gene flow is lacking in many important species such as <em>Cannabis</em> <em>sativa </em>(<em>C. sativa</em>), one of the oldest known crops to be cultivated by humans worldwide. We generated whole genome resequencing data across diverse samples of feralized (escaped domesticated lineages) and domesticated lineages of <em>C. sativa</em>. We performed analyses to examine population structure, and genome wide scans for FST, balancing selection, and positive selection. Our analyses identified evidence for sub-population structure and further support the Asian origin hypothesis of this species. Feral plants sourced from the U.S. exhibited broad regions on chromosomes 4 and 10 with high <span>𝐹̅</span>ST which may indicate chromosomal inversions maintained at high frequency in this sub-population. Both our balancing and positive selection analyses identified loci that may reflect differential selection for traits favored by natural selection and artificial selection in feral versus domesticated sub-populations. In the U.S. feral sub-population, we found six loci related to stress response under balancing selection and one gene involved in disease resistance under positive selection, suggesting local adaptation to new climates and biotic interactions. In the marijuana sub-population, we identified the gene <em>SMALLER TRICHOMES</em> <em>WITH VARIABLE BRANCHES 2 </em>to be under positive selection which suggests artificial selection for increased tetrahydrocannabinol yield. Overall the data generated, and results obtained from our study help to form a better understanding of the evolutionary history in <em>C. sativa</em>.</p>
Supplementary material 4 from: Hagen BL, Kumschick S (2018) The relevance of using various scoring schemes revealed by an impact assessment of feral mammals. NeoBiota 38: 37-75. https://doi.org/10.3897/neobiota.38.23509
Detailed SEICAT assessments (Table S4) : Explanation note: A summary of the impact assessment using the Socio-Economic Impact Classification for Alien Taxa (SEICAT). Impact scores, from highest to lowest are Massive (MV), Major (MR), Moderate (MO), Minor (MN) and Minimal Concern (MC). Full reference details are given in Appendix 2. Region indicates whether the impact was found on islands or the mainland.
Supplementary material 2 from: Hagen BL, Kumschick S (2018) The relevance of using various scoring schemes revealed by an impact assessment of feral mammals. NeoBiota 38: 37-75. https://doi.org/10.3897/neobiota.38.23509
Detailed GISS assessments (Table S2) : Explanation note: Details of the environmental and socio-economic impact assessment using the Generic Impact Scoring System (GISS). Full reference details are given in Appendix 2. Region indicates whether the impact was found on islands or the mainland.
Supplementary material 1 from: Hagen BL, Kumschick S (2018) The relevance of using various scoring schemes revealed by an impact assessment of feral mammals. NeoBiota 38: 37-75. https://doi.org/10.3897/neobiota.38.23509
Differences between scoring schemes (Table S1) : Explanation note: Scoring differences for GISS, EICAT and SEICAT. This table was adapted from Kumschick et al. (2016) and Bacher et al. (2017). The numbers in the top column refer to the GISS scoring classifications, whereas the terms 'massive' to 'minimal concern' refer to EICAT and SEICAT scoring classifications.
Supplementary material 3 from: Hagen BL, Kumschick S (2018) The relevance of using various scoring schemes revealed by an impact assessment of feral mammals. NeoBiota 38: 37-75. https://doi.org/10.3897/neobiota.38.23509
Detailed EICAT assessments (Table S3) : Explanation note: A summary of the impact assessment using the Environmental Impact Classification for Alien Taxa (EICAT). Impact scores, from highest to lowest are Massive (MV), Major (MR), Moderate (MO), Minor (MN) and Minimal Concern (MC). Full reference details are given in Appendix 2. Region indicates whether the impact was found on islands or the mainland.
Data from: Linking genetic diversity and temporal fluctuations in population abundance of the introduced feral cat (Felis silvestris catus) on the Kerguelen Archipelago.
Linking temporal variations of genetic diversity, including allelic richness and heterozygosity, and spatio-temporal fluctuations in population abundance has emerged as an important tool for understanding demographic and evolutionary processes in natural populations. This so-called 'genetic monitoring' was conducted across 12 consecutive years (1996-2007) at three sites for the feral cat, introduced onto the Kerguelen Archipelago fifty years ago. Temporal changes in allelic richness and heterozygosity at 18 microsatellite DNA loci were compared to temporal changes in the adult population abundance index, obtained by typical demographic monitoring. No association was found at the island spatial scale but we observed an association between genetic diversity and adult population indices from year to year within each study site. More particularly, the magnitude of successive increases or decreases in the adult population abundance index appeared to be the major factor linking the trajectories of genetic diversity and adult population abundance indices. Natal dispersal and/or local recruitment, both facilitated by high juvenile survival when the adult population size is small, are proposed as the major demographic processes contributing to such an observed pattern. Finally, we suggested avoiding the use of the harmonic mean as an estimator of long-term population size to study the relationships between demographic fluctuations and heterozygosity in populations characterized by strong multi-annual density fluctuations.
Data from: Feral cats are better killers in open habitats, revealed by animal-borne video
One of the key gaps in understanding the impacts of predation by small mammalian predators on prey is how habitat structure affects the hunting success of small predators, such as feral cats. These effects are poorly understood due to the difficulty of observing actual hunting behaviours. We attached collar-mounted video cameras to feral cats living in a tropical savanna environment in northern Australia, and measured variation in hunting success among different microhabitats (open areas, dense grass and complex rocks). From 89 hours of footage, we recorded 101 hunting events, of which 32 were successful. Of these kills, 28% were not eaten. Hunting success was highly dependent on microhabitat structure surrounding prey, increasing from 17% in habitats with dense grass or complex rocks to 70% in open areas. This research shows that habitat structure has a profound influence on the impacts of small predators on their prey. This has broad implications for management of vegetation and disturbance processes (like fire and grazing) in areas where feral cats threaten native fauna. Maintaining complex vegetation cover can reduce predation rates of small prey species from feral cat predation.
Persistence of an endangered native duck, feral mallards, and multiple hybrid swarms across the main Hawaiian Islands
Interspecific hybridization is recognized as an important process in the evolutionary dynamics of both speciation and the reversal of speciation. However, our understanding of the spatial and temporal patterns of hybridization that erode versus promote species boundaries is incomplete. The endangered, endemic koloa maoli (or Hawaiian duck, Anas wyvilliana) is thought to be threatened with genetic extinction through ongoing hybridization with an introduced congener, the feral mallard (A. platyrhynchos). We investigated spatial and temporal variation in hybrid prevalence in populations throughout the main Hawaiian Islands, using genomic data to characterize population structure of koloa, quantify the extent of hybridization, and compare hybrid proportions over time. To accomplish this, we genotyped 3,308 double-digest restriction-site-associated DNA (ddRAD) loci in 425 putative koloa, mallards, and hybrids from populations across the main Hawaiian Islands. We found that despite a population decline in the last century, koloa genetic diversity is high. There were few hybrids on the island of Kauaʻi, home to the largest population of koloa. By contrast, we report that sampled populations outside of Kauaʻi can now be characterized as hybrid swarms, in that all individuals sampled were of mixed koloa × mallard ancestry. Further, there is some evidence that these swarms are stable over time. These findings demonstrate spatial variation in the extent and consequences of interspecific hybridization, and highlight how islands or island-like systems with small population sizes may be especially prone to genetic extinction when met with a congener that is not reproductively isolated.
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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.