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18 results for “ex situ management”
Figure 5 in Development of predictive models for determining fetal age-at-length in belugas (Delphinapterus leucas) and their application toward in situ and ex situ population management
Figure 5. Illustration of the linear relationships between fetal age and growth measurements of biparietal diameter (BPD: top graph), thoracic diameter (TD: middle graph) and thoracic circumference (TC: bottom graph) in belugas.
Figure 4 in Development of predictive models for determining fetal age-at-length in belugas (Delphinapterus leucas) and their application toward in situ and ex situ population management
Figure 4. Comparisons of regression curves of TL growth during the first (●) and second half (○) of gestation (top graph) and the early (●), mid (○) and late (▲) pregnancy (bottom graph). The slopes of the regression lines for first half of gestation (F = 63.31, P <0.0001, df1 = 1, df2 = 33) and for early (F = 50.05, P <0.0001, df1 = 1, df2 = 37) and mid pregnancy (F = 135.04, P <0.0001, df1 = 1, df2 = 32) were different than those for the second half of gestation and late pregnancy, respectively. Note that the animals double in length during late pregnancy (315–473 d).
Figure 3 in Development of predictive models for determining fetal age-at-length in belugas (Delphinapterus leucas) and their application toward in situ and ex situ population management
Figure 3. Individual growth rate data from three animals (Animal 1, 2, 3). Regression line slopes during the first two-thirds of pregnancy (top graph) were similar (F = 0.48, P = 0.62, df1 = 2, df2 =18), while regression slopes where different (F = 15.13, P = 0.03, df1 = 2, df2 =3) from the second half to term. Animal 1 (▲) did not have any TL data beyond the first half of gestation so TL length data were used from the farthest in gestation and then again at term. Note that while growth rates were similar during the first two-thirds of pregnancy, fetuses were already different in size when initially detected.
Figure 2 in Development of predictive models for determining fetal age-at-length in belugas (Delphinapterus leucas) and their application toward in situ and ex situ population management
Figure 2. Fetal growth curve comparison illustrating different growth rates resulting in wide range in estimated gestation length as compared to known gestation length determined in this study. Data from Heide-Jørgensen and Teilmann (1994; dotted line) predicts a gestation length of 310 d for a 150 cm calf and similar to our study used a 2nd order polynomial regression to describe their data. Kleinenberg et al. ([1964] 1969: dashed line) developed a curve of the average monthly embryo/fetal growth. They did not provide the curve, only the predicted age at TL, which we then used to fit to a growth curve, which predicts 150 cm calf as 338 d.
Figure 1 in Development of predictive models for determining fetal age-at-length in belugas (Delphinapterus leucas) and their application toward in situ and ex situ population management
Figure 1. Ultrasonographic images of beluga fetuses. All images have yellow caliper lines used to measure dimensions. Biparietal diameter (A, B) at two different stages of gestation show the ovoid shaped skull and echo produced from falx (arrows) located midline between the parietal bones (arrowheads). The thoracic diameter (C) as measured between the yellow caliper marks (arrowheads) on the lateral side of the fetal thorax (d1 = 6.66 cm) at the level of the heart (white arrow) and thoracic circumference (c = 24.04 cm) determined by using the elliptical measurement caliper function to include the dorsal to ventral diameter (d2 = 8.67 cm). The total length of a fetus (D) which is bent in utero, thus requiring the addition of two separate measurements (arrowheads), 1) 8.38 cm from the cranial most aspect of the skull to mid abdomen and 2) 6.91 cm from mid abdomen to distal most portion of the peduncle for a total length of 15.29 cm.
Figure 8 in Is there a chance for conservation breeding? Ex situ management, reproduction, and early life stages of the Harlequin toad Atelopus flavescens Duméril & Bibron, 1841 (Amphibia: Anura: Bufonidae)
Figure 8. Individual recognition of a male Atelopus flavescens based on color pattern, but note the change in color (photographs taken 12 July 2009 and 31 July 2011, respectively). Photographs by D. Karbe.
Figure 7 in Is there a chance for conservation breeding? Ex situ management, reproduction, and early life stages of the Harlequin toad Atelopus flavescens Duméril & Bibron, 1841 (Amphibia: Anura: Bufonidae)
Figure 7. Color patterns of Atelopus flavescens at the amphibian breeding unit at the Cologne Zoo: Four females (above) and males (below) in ventral and dorsal views. Photographs by D. Karbe.
Figure 6 in Is there a chance for conservation breeding? Ex situ management, reproduction, and early life stages of the Harlequin toad Atelopus flavescens Duméril & Bibron, 1841 (Amphibia: Anura: Bufonidae)
Figure 6. Total length (mm) of larger tadpole of Atelopus flavescens from first clutch in relation to age in days; water temperature 22-24 °C.
Figure 4 in Is there a chance for conservation breeding? Ex situ management, reproduction, and early life stages of the Harlequin toad Atelopus flavescens Duméril & Bibron, 1841 (Amphibia: Anura: Bufonidae)
Figure 4. Hatched larvae of Atelopus flavescens (from first egg deposition): (A) - (B) hatchlings at Gosner stage 20 (13 December 2010), (C) lateral view of tadpole at stages 24-25 (27 December 2010, 22 days after egg deposition), (D) ventral view of tadpole at stage 25 (3 January 2011, 29 days after egg deposition). Photographs by D. Karbe.
Figure 3 in Is there a chance for conservation breeding? Ex situ management, reproduction, and early life stages of the Harlequin toad Atelopus flavescens Duméril & Bibron, 1841 (Amphibia: Anura: Bufonidae)
Figure 3. First clutch of Atelopus flavescens at the amphibian breeding unit at the Cologne Zoo: (A) freshly deposited spawn under water surface on stones or filamentous algae (5 to 6 December 2010), (B) cream-colored eggs one day after deposition (6 December 2010), (C) developing embryos at Gosner stage <18 (9 December 2010), (D) embryos at stage 19 (10 December 2010). Photographs by D. Karbe.
Figure 2 in Is there a chance for conservation breeding? Ex situ management, reproduction, and early life stages of the Harlequin toad Atelopus flavescens Duméril & Bibron, 1841 (Amphibia: Anura: Bufonidae)
Figure 2. Atelopus flavescens at the amphibian breeding unit at the Cologne Zoo: (A) adult male, (B) calling male, and (C) couple in amplexus. Photograph (A) (B) by T. Ziegler and (C) by D. Karbe.
Figure 1 in Is there a chance for conservation breeding? Ex situ management, reproduction, and early life stages of the Harlequin toad Atelopus flavescens Duméril & Bibron, 1841 (Amphibia: Anura: Bufonidae)
Figure 1. Atelopus flavescens terraria in the amphibian breeding unit at the Cologne Zoo from different perspectives (A) - (D); both terraria have artificial streams in the foreground. Photographs by D. Karbe.
Figure 5 in Is there a chance for conservation breeding? Ex situ management, reproduction, and early life stages of the Harlequin toad Atelopus flavescens Duméril & Bibron, 1841 (Amphibia: Anura: Bufonidae)
Figure 5. Tadpoles of Atelopus flavescens: (A) ventral view of larva at Gosner stage 28 (22 February 2011, 79 days after egg deposition; from first clutch; larger larva), (B) lateral view of tadpole at stages 34-36 (22 April 2011, 96 days after egg deposition; from second clutch), (C) ventral view of tadpole at stage 41 (26 April 2011, 100 days after egg deposition; from second clutch), (D) tadpole at stage 42 (15 April 2011, 131 days after egg deposition; smaller larva). Photographs by D. Karbe.
Data from: implications of methodologies for integrating empirical kinships into ex situ population management using PMx: a case study of Baer’s Pochard (Aythya baeri) in North America
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Predictive genetic plan for a captive population of the Chinese goral (Naemorhedus griseus) and prescriptive action for ex situ and in situ conservation management in Thailand
<p>Captive breeding programs for endangered species can increase population numbers for eventual reintroduction to the wild. Captive populations are typically small and isolated, which results in inbreeding and reduction of genetic variability, and may lead to an increased risk of extinction. The Omkoi Wildlife Breeding Center maintains the only Thai captive Chinese goral (<i>Naemorhedus griseus</i>) population, and has plans to reintroduce individuals into natural isolated populations. Genetic variability was assessed within the captive population using microsatellite data. Although no bottleneck was observed, genetic variability was low (allelic richness = 7.091 ± 0.756, <i>H</i><sub>e</sub> = 0.455 ± 0.219; <i>H</i><sub>e</sub> < <i>H</i><sub>o</sub>) and 11 microsatellite loci were informative that likely reflect inbreeding. Estimates of small effective population size and limited numbers of founders, combined with wild-born individuals within subpopulations, tend to cause reduction of genetic variability over time in captive programs. This leads to low reproductive fitness and limited ability to adapt to environmental change, thereby increasing the risk of extinction. Management of captive populations as evolutionarily significant units with diverse genetic backgrounds offers an effective strategy for population recovery. Relocation of individuals among subpopulations, or introduction of newly captured wild individuals into the captive program will help to ensure the future security of Chinese goral. Implications for future conservation actions for the species are discussed herein.</p>
Data from: Distinguishing the victim from the threat: SNP‐based methods reveal the extent of introgressive hybridization between wildcats and domestic cats in Scotland and inform future in situ and ex situ management options for species restoration
The degree of introgressive hybridisation between the Scottish wildcat and domestic cat has long been suspected to be advanced. Here we use a 35-SNP-marker test, designed to assess hybridisation between wildcat and domestic cat populations in Scotland, to assess a database of 265 wild-living and captive cat samples, and test the assumptions of the test using 3097 SNP markers generated independently in a subset of the data using ddRAD. We discovered that despite increased genetic resolution provided by these methods, wild-living cats in Scotland show a complete genetic continuum or hybrid swarm structure when judged against reference data. The historical population of wildcats, although hybridised, clearly groups at one end of this continuum, as does the captive population of wildcats. The interpretation of pelage scores against nuclear genetic data continues to be problematic. This is probably because of a breakdown in linkage disequilibrium between wildcat pelage genes as the two populations have become increasingly mixed, meaning that pelage score or SNP score alone are poor diagnostic predictors of hybrid status. Until better tools become available, both should be used jointly, where possible, when making management decisions about individual cats. We recommend that the conservation community in Scotland must now define clearly what measures are to be used to diagnose a wildcat in the wild in Scotland, if future conservation action is to be effective.
Data from: Distinguishing the victim from the threat: SNP‐based methods reveal the extent of introgressive hybridization between wildcats and domestic cats in Scotland and inform future in situ and ex situ management options for species restoration
Open the record for dataset details and reuse information.
Predictive genetic plan for a captive population of the Chinese goral (Naemorhedus griseus) and prescriptive action for ex situ and in situ conservation management in Thailand
Open the record for dataset details and reuse information.
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Allen Brain Atlas
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DANDI Archive for NWB datasets
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International Brain Laboratory public data
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OpenNeuro
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