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113 results for “Reindeer”
Data for: Harvest and decimation affect genetic drift and the effective population size in wild reindeer
<p>Harvesting and culling are methods used to monitor and manage wildlife diseases. An important consequence of these practices is a change in the genetic dynamics of affected populations that may threaten their long-term viability. The effective population size (N<sub>e</sub>) is a fundamental parameter for describing such changes as it determines the amount of genetic drift in a population. Here, we estimate N<sub>e</sub> of a harvested wild reindeer population in Norway. Then we use simulations to investigate the genetic consequences of management efforts for handling a recent spread of chronic wasting disease, including increased adult male harvest and population decimation. The N<sub>e</sub>/N ratio in this population was found to be 0.124 at the end of the study period, compared to 0.239 in the preceding 14-year period. The difference was caused by increased harvest rates with a high proportion of adult males (older than 2.5 years) being shot (15.2 % in 2005-2018 and 44.8 % in 2021). Increased harvest rates decreased N<sub>e</sub> in the simulations, but less sex-biased harvest strategies had a lower negative impact. For harvest strategies that yield stable population dynamics, shifting the harvest from calves to adult males and females increased N<sub>e</sub>. Population decimation always resulted in decreased genetic variation in the population, with higher loss of heterozygosity and rare alleles with more severe decimation or longer periods of low population size. A very high proportion of males in the harvest had the most severe consequences for the loss of genetic variation. This study clearly shows how the effects of harvest strategies and changes in population size interact to determine the genetic drift of a managed population. The long-term genetic viability of wildlife populations subject to disease will also depend on the population impacts of the disease and how these interact with management actions.</p>
The efficacy of wildlife fences for keeping reindeer outside a chronic wasting disease risk area
<p>Data to</p> <p>"The efficacy of wildlife fences for keeping reindeer outside a chronic wasting disease risk area"</p> <p>accepted in Ecological Solutions and Evidence</p>
Svalbard reindeer winter diets (1995–2012) dataset
<p>Arctic ecosystems are changing dramatically with warmer and wetter conditions resulting in complex interactions between herbivores and their forage. We investigated how Svalbard reindeer (<em>Rangifer tarandus platyrhynchus</em>) modify their late winter diets in response to long-term trends and interannual variation in forage availability and accessibility. By reconstructing their diets and foraging niches over a 17-year period (1995–2012) using serum δ<sup>13</sup>C and δ<sup>15</sup>N values, we found strong support for a temporal increase in the proportions of graminoids in the diets with a concurrent decline in the contributions of mosses. This dietary shift corresponds with graminoid abundance increases in the region and was associated with increases in population density, warmer summer temperatures and more frequent rain-on-snow (ROS) in winter. In addition, the variance in isotopic niche positions, breadths and overlaps also supported a temporal shift in the foraging niche and a dietary response to extreme ROS events. Our long-term study highlights the mechanisms by which winter and summer climate changes cascade through vegetation shifts and herbivore population dynamics to alter the foraging niche of Svalbard reindeer. Although i<span>t has been anticipated that climate changes in the Svalbard region of the Arctic would be detrimental to this unique ungulate</span>, our study suggests that environmental change is in a phase where conditions are improving for this subspecies at the northernmost edge of the <em>Rangifer</em> distribution.</p>
Figure 1 in A Nearctic parasite in a Palearctic host: Parelaphostrongylus andersoni (Nematoda; Protostrongylidae) infecting semi-domesticated reindeer in Alaska
Figure 1. Map of the Seward Peninsula, Alaska, showing semi-domesticated reindeer herd ranges including the Kakarak herd (bold), and reindeer herd loss to Western Arctic caribou herd; and the western limits of caribou migration from 1989 to 2000 (modified from Finstad et al. (2006) and Rattenbury et al. (2009)).
Fig. 2 in Apparent fatal winter tick (Dermacentor albipictus) infestation in captive reindeer (Rangifer tarandus)
Fig. 2. Dorsal (A) and ventral view (B) of an adult female Dermacentor albipictus collected from captive reindeer. Inset image shows large goblet cells on the spiracular plate.
Fig. 1 in Pathology, clinical signs, and tissue distribution of Toxoplasma gondii in experimentally infected reindeer (Rangifer tarandus)
Fig. 1. Brain squash picture of T. gondii tissue cyst of reindeer 2 brain visualized on compound microscopy (60×).
Fig. 2 in Pathology, clinical signs, and tissue distribution of Toxoplasma gondii in experimentally infected reindeer (Rangifer tarandus)
Fig. 2. Histological section of reindeer 3 diaphragm containing a T. gondii cyst visualized at 100× with oil immersion after immunohistochemical stain.
Fig. 3 in Elaphostrongylus and Dictyocaulus infections in Norwegian wild reindeer and red deer populations in relation to summer pasture altitude and climate
Fig. 3. Calculated average altitude above sea level (points) with standard deviation (thicker grey line) of the main summer pasture area of six wild reindeer and two wild red deer populations in South Norway sampled for parasitological studies 2012–2014. The calculation was based upon GPS-positions recorded during June, July and August. The recorded min and max altitudes are indicated by the ends of the black line. Reindeer populations (No): 14 Nordfjella, 2 Snøhetta, 19 Setesdal Ryfylke, 1 Forollhogna, 6 Rondane, 20 Setesdal Austhei. Red deer populations (No): 24 Ørsta, 25 Kvinnherad.
Fig. 1 in Elaphostrongylus and Dictyocaulus infections in Norwegian wild reindeer and red deer populations in relation to summer pasture altitude and climate
Fig. 1. Map of South Norway showing the location of the 23 Norwegian wild tundra reindeer populations (No 1–23). The six populations included in the present study (No 1, 2, 6, 14, 19, 20) are marked with brighter tan. The location of two wild red deer municipalities studied (No 24, 25) are marked in green. (For interpretation of the references to color in this figure legend, the reader is referred to the Web version of this article.)
Fig. 5 in Elaphostrongylus and Dictyocaulus infections in Norwegian wild reindeer and red deer populations in relation to summer pasture altitude and climate
Fig. 5. Calculated mean temperature (̊C) and monthly rainfall (mm) for June–August at the average altitude of the main summer pasture areas for eight wild reindeer and red deer populations sampled for parasitological studies 2012–2014. The data represent the five summers prior to sampling. The range and average (horizontal bar) of mean monthly temperature (left y-axis) and rainfall (right y-axis) are shown by red and blue lines respectively. Reindeer populations (No): 14 Nordfjella, 2 Snøhetta, 19 Setesdal Ryfylke, 1 Forollhogna, 6 Rondane, 20 Setesdal Austhei. Red deer populations (No): 24 Ørsta, 25 Kvinnherad. (For interpretation of the references to color in this figure legend, the reader is referred to the Web version of this article.)
Fig. 2 in Elaphostrongylus and Dictyocaulus infections in Norwegian wild reindeer and red deer populations in relation to summer pasture altitude and climate
Fig. 2. Example of Kernel Density Analysis, visualizing the main grazing area of radio-collared females in the wild reindeer population in Nordfjella during June, July and August. The darker the color, the larger number of GPS positions recorded. The outer limits of the area are marked with a dark line. (For interpretation of the references to color in this figure legend, the reader is referred to the Web version of this article.)
Fig. 3 in High winter loads of Oestrid larvae and Elaphostrongylus rangiferi are associated with emaciation in wild reindeer calves
Fig. 3. Visualization of fat reserves in the bone marrow of femur (row 1), knee joint (row 2), vertebral canal (row 3), orbital cavity (row 4), and heart surface (row 5). The three categories used are illustrated from left to right: clearly visible white and stiff fat (+); low amounts of visible fat with a soft consistency (+÷); absence of visible fat (serous adipose atrophy) (÷). All figures are from wild reindeer calves killed on Hardangervidda in spring 2015, except for the heart to the bottom right which is from a moose that died from winter starvation.
Fig. 6 in High winter loads of Oestrid larvae and Elaphostrongylus rangiferi are associated with emaciation in wild reindeer calves
Fig. 6. Photograph from the inside of the skin showing Hypoderma tarandi larvae removed from the lower part of the back of a calf killed on Hardangervidda in spring 2015.
Fig. 9 in High winter loads of Oestrid larvae and Elaphostrongylus rangiferi are associated with emaciation in wild reindeer calves
Fig. 9. Calculated mean air temperature (◦C) in the main summer pasture area of the Hardangervidda wild reindeer population for individual summers (June–August) 1989–2018. The summers of 2014 and 2015 are marked with a black circle. The dotted horizontal line shows the mean (7.4 ◦C) for the 30- year-period.
Fig. 5 in High winter loads of Oestrid larvae and Elaphostrongylus rangiferi are associated with emaciation in wild reindeer calves
Fig. 5. Cephenemyia trompe larvae in the pharynx/nasopharynx of a calf killed on Hardangervidda in spring 2015. Note the paired, swollen retropharyngeal lymph nodes (Ln).
Fig. 4 in High winter loads of Oestrid larvae and Elaphostrongylus rangiferi are associated with emaciation in wild reindeer calves
Fig. 4. Translucent white first stage Cephenemyia trompe larvae (1 mm) in the nasal mucosa of a calf killed on Hardangervidda in autumn 2014.
Fig. 10 in High winter loads of Oestrid larvae and Elaphostrongylus rangiferi are associated with emaciation in wild reindeer calves
Fig. 10. Calculated number of summer days (June–August) with a mean air temperature ≥12 ◦C in the main summer pasture area of the wild reindeer population on Hardangervidda. The figure shows the mean and range for the 30-year period 1989–2018, and the mean for individual years 2014 and 2015 as well as for the five years with a higher mean temperature than in 2014.
Fig. 8 in High winter loads of Oestrid larvae and Elaphostrongylus rangiferi are associated with emaciation in wild reindeer calves
Fig. 8. Group of adult hair-thin, about 3–5 cm long Elahostrongylus rangiferi nematodes in the muscle fascia of a calf killed on Hardangervidda in spring 2015.
Fig. 1 in High winter loads of Oestrid larvae and Elaphostrongylus rangiferi are associated with emaciation in wild reindeer calves
Fig. 1. Map of southern Norway showing the location of the 24 Norwegian wild tundra reindeer populations. The Hardangervidda population (No. 16) is marked with brighter tan.
Fig. 2 in High winter loads of Oestrid larvae and Elaphostrongylus rangiferi are associated with emaciation in wild reindeer calves
Fig. 2. Kernel Density Analysis, visualizing the main pasture area of radio-collared females in the wild reindeer population in Hardangervidda during June, July, and number of GPS positions recorded. Calculated center at UTM 32V: 426706–6650377 and average altitude at 1283m. The center in the previously used summer area with an asterisk. The red lines represent summer trails for hikers marked by the Norwegian Tourist Association. (For interpretation of the references to color in this figure of this article.)
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