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1,513 results for “disturbance”
Rodent ectoparasite diversity in response to anthropogenic disturbance
<p>Rodents are important hosts for ectoparasites such as fleas, ticks, and mites, which means they are also important intermediate hosts for many zoonotic diseases. As anthropogenic environments bring humans and rodents into closer contact, an understanding of host-ectoparasite ecology is essential to predict and manage disease spillover risks. We aimed to understand how disturbances in vegetation cover affect rodent ectoparasite diversity, prevalence, spatial segregation, host (i.e. sex, genus, size, habitat domain), and environmental (i.e. vegetation structure, forest cover, rainfall) variables in the state of Michoacan, Mexico. We compared these variables by trapping rodents in five paired disturbed (reduced vegetation cover, regular human presence) and undisturbed (no reduction in vegetation cover, no human presence) sites in the summer and autumn of 2022. From 108 trapped rodents, we collected 123 ectoparasites on 34 individuals. We found no difference in rodent diversity, ectoparasite diversity, or ectoparasite prevalence between disturbed and undisturbed sites. However, ground-dwelling and male rodents had a higher probability of carrying ectoparasites than arboreal and female rodents. Rodents with ectoparasites were not spatially clustered; rather, they were randomly distributed across trapping grids. We also identified two rodent genera (<em>Rattus </em>and <em>Sigmodon</em>) that carry ectoparasites of medical importance and that are in close contact with humans. Our results highlight the necessity of constant monitoring of rodents, ectoparasites, and their associated transmittable diseases. Assessing these interactions and how they are affected by anthropogenic disturbance could better inform management decisions and support the need for rodent conservation programs in the area.</p>
Digital repository for: Large-scale forest disturbance and associated management shape bird communities in Central European spruce forests
<p>Repository containing R-script and data to reproduce analysis and main figures on the effect of large-scale forest disturbance and associated pre- and post-disturbance management on bird communities in the Harz Mountains, Germany.</p> <p>R-script includes:</p> <ul> <li>indicator species analysis (R package indicspecies; Cáceres & Legendre, 2009)</li> <li>non-metric multidimensional scaling (R package vegan; Oksanen et al., 2016)</li> <li>rarefaction- and extrapolation of Hill numbers (R package iNEXT; Hsieh et al., 2019)</li> <li>multi-species community distance sampling (R package sp Abundance; Doser et al., 2023)</li> </ul> <p>Attached files:</p> <ul> <li><strong>bird_data_Graser_et_al.csv </strong>(row data of bird species point counts per distance category)</li> <li><strong>bird_data_abundance_100_Graser_et_al.csv </strong>(abundance of species per sampling site, summed up over all four sampling repeats only considering detected individuals up to 100 m around the sampling point)</li> <li><strong>siteCovs_Graser_et_al.csv</strong> (environmental variables for each sampling point)</li> <li><strong>A_species_matrix_100_new_Graser_et_al.csv</strong> (species-site matrix of <strong>bark-beetle disturbance, unlogged </strong>sites for rarefaction and extrapolation, species number summed up over all four sampling repeats only considering detected individuals up to 100 m around the sampling point)</li> <li><strong>B_species_matrix_100_new_Graser_et_al.csv </strong>(species-site matrix of <strong>windthrow disturbance, unlogged </strong>sites for rarefaction and extrapolation, species number summed up over all four sampling repeats only considering detected individuals up to 100 m around the sampling point)</li> <li><strong>C_species_matrix_100_new_Graser_et_al.csv </strong>(species-site matrix of <strong>bark-beetle/windthrow disturbance, underplanted, unlogged </strong>sites for rarefaction and extrapolation, species number summed up over all four sampling repeats only considering detected individuals up to 100 m around the sampling point)</li> <li><strong>D_species_matrix_100_new_Graser_et_al.csv </strong>(species-site matrix of <strong>bark-beetle /windthrow disturbance, salvage-unlogged </strong>sites for rarefaction and extrapolation, species number summed up over all four sampling repeats only considering detected individuals up to 100 m around the sampling point)</li> <li><strong>E_species_matrix_100_new_Graser_et_al.csv </strong>(species-site matrix of <strong>bark-beetle /windthrow disturbance, underplanted, salvage-unlogged </strong>sites for rarefaction and extrapolation, summed up over all four sampling repeats only considering detected individuals up to 100 m around the sampling point)</li> <li><strong> F_species_matrix_100_new_Graser_et_al.cs</strong>v (species-site matrix of <strong>mature spruce plantation </strong>sites for rarefaction and extrapolation, species number summed up over all four sampling repeats only considering detected individuals up to 100 m around the sampling point)</li> <li><strong>msHDS_bird_data_management_model_Graser_et_al.rds</strong> (R-data set for multi-species community distance sampling of the effect of different pre- and post-disturbance management groups)</li> <li><strong>msHDS_bird_data_stand_age_model_Graser_et_al.rds </strong>(R-data set for multi-species community distance sampling of the effect of post-disturbance forest succession)</li> </ul> <p>A more detailed description of the data can be found in the README.txt document.</p> <p><span>References:</span></p> <p><span>Cáceres, M. D., & Legendre, P. (2009). </span><span>Associations between species and groups of sites: Indices and statistical inference. <em>Ecology</em>, <em>90</em>(12), 3566–3574. https://doi.org/10.1890/08-1823.1</span></p> <p><span>Doser, J. W., Finley, A. O., Kéry, M., & Zipkin, E. F. (2023). spAbundance: An R package for single‐species and multi‐species spatially explicit abundance models. <em>Methods in Ecology and Evolution</em>, <em>15</em>(6), 1024–1033. https://doi.org/10.1111/2041-210X.14332</span></p> <p><span>Hsieh, T. C., Ma, K. H., & Chao, A. (2019). <em>iNEXT-package: Interpolation and extrapolation for species diversity</em>. https://cran.r-project.org/web/packages/iNEXT/vignettes/Introduction.html</span></p> <p><span>Oksanen, J., Blanchet, F. G., Kindt, R., Legendre, P., O’hara, R. B., Simpson, G. L., Solymos, P., Stevens, M. H. H., Wagner, H., Minchin, P. R., Gavin, L., & Henry, H. (2016). Vegan: Community ecology package. R package version 1.17-4. <em>Http://CRAN. R-Project. </em></span><em><span>Org/Package=vegan</span></em><span>.</span></p> <p></p> <p></p>
Gradient winds and neutral flow dawn-dusk asymmetry in the auroral oval during geomagnetically disturbed conditions (data files)
<p>Data files with wind profiles used to generate figures in the paper entitled "Gradient winds and neutral flow dawn-dusk asymmetry in the auroral oval during geomagnetically disturbed conditions"</p>
Zooplankton recovery from a whole‐lake disturbance: Examining roles of abiotic factors, biotic interactions, and traits
<p>Community assembly following disturbance is a key process in determining the composition and function of the future community. However, replicated studies of community assembly at whole ecosystem scales are rare. Here, we describe a series of whole-lake experiments in which the recovery of zooplankton communities was tracked following an ecosystem-scale disturbance, i.e., application of the piscicide, rotenone. Using a BACI design, fourteen lakes in eastern Washington were studied: seven lakes were treated with rotenone, while seven lakes acted as reference systems. Each lake was monitored up to six months before and one to two years after the rotenone treatments. Zooplankton samples and environmental measurements were collected approximately monthly from each lake. Community responses following disturbance were assessed using metrics of abundance, diversity, and community composition, as well as taxonomic group abundance. Zooplankton recovery was also assessed using species traits related to habitat, feeding mode, trophic level, body size, and life history. In addition to patterns of recovery, potential mechanisms were explored relating to abiotic conditions, biotic interactions, and traits. There were steep declines in the abundance (average across years: 99%) and diversity (average across years: 75%) of the zooplankton community following rotenone treatment. Although abundance had recovered by the second year of the study, community diversity had not fully recovered after two years. Communities from rotenone lakes appeared to be compositionally recovered within about eight months following disturbance. Cyclopoid copepods were typically the first group to recover, and remained dominant for a few months, whereas cladocerans recovered more slowly, typically within ~6-7 months following rotenone. Calanoid copepods were not fully recovered two years after rotenone treatment. Traits related to body size and feeding mode were associated with the zooplankton communities following rotenone treatment. We failed to observe significant spatial synchrony in recovery patterns of zooplankton across lakes, though we did observe significant synchrony of zooplankton taxonomic groups within lakes. These findings suggest that traits related to ecological function, and to a lesser extent, biotic and abiotic factors, as well as characteristics of the disturbance itself, may be important in helping to understand recovery processes. </p>
Food web rewiring drives long-term compositional differences and late-disturbance interactions at the community level
<p><strong>Abstract</strong></p> <p>Ecological communities are constantly exposed to multiple natural and anthropogenic disturbances. Multivariate composition (if recovered) has been found to need significantly more time to be regained after pulsed disturbance compared to univariate diversity metrics and functional endpoints. However, the mechanisms driving the different recovery times of communities to single and multiple disturbances remain unexplored. Here, we apply for the first time quantitative ecological network analyses to try to elucidate the mechanisms driving long-term community composition dissimilarity and late-stage disturbance interactions at the community level. For this, we evaluate the effects of two pesticides, nutrients enrichment and their interactions in outdoor mesocosms containing a complex freshwater community. We found changes in interactions strength to be strongly related to compositional changes and identified post-disturbance interaction strength rewiring to be responsible for most of the observed compositional changes. Additionally, we found pesticides interactions to be significant in the long term only when both interactions strength and food web architecture are reshaped by the disturbances. We suggest that quantitative network analysis has the potential to unveil ecological processes that prevent long-term community recovery.</p> <p><strong>Significance Statement</strong></p> <p>Multiple anthropogenic disturbances affect the structure and functioning of communities. Recent evidence highlighted that, after pulse disturbance, the functioning a community performs may be recovered fast due to functional redundancy, whereas community multivariate composition needs longer time. Yet, the mechanisms that drive the different community recovery times have not been quantified empirically. We use quantitative food web analysis to assess the influence of species interactions on community recovery. We found species interactions strength to be the main mechanism driving differences between structural and functional recovery. Additionally, we show that interactions between multiple disturbances appear in the long term only when both species interaction strength and food web architecture change significantly.</p> <p>Please see the "readme" sheet in the datafile for a description of the file structure and treatments abreviations.</p>
Dataset of habitat quality does not predict animal population abundance on frequently disturbed landscapes
<p>The data presented here are related to the research article entitled "Habitat quality does not predict animal population abundance on frequently disturbed landscapes". Using an individual-based model, we simulated movement of theoretical individuals in a dynamically disturbed landscape and quantified the error of predicting population spatial relative abundance using an habitat model. This dataset provides the Earth Mover's Distance (EMD) as prediction error measure obtained in simulations with varying individual step length and disturbance frequency.</p>
Fig. 1 in Dynamics Of Mouse-Like Rodent Communities In Anthropogenically Disturbed Territories Of The Southeast Of Western Siberia (Kemerovo Region, Russia)
Fig. 1. The dynamics of similarity of small mammal populations in deforested zones compared to the initial population in taiga (using the Czekanowsky-SØrensen coefficient calculated for species' percentage in the community).
Contrasting effects of anthropogenic disturbance on the interaction among sympatric carnivores
Interaction among species is central to the stability of community structure. However, anthropogenic pressures alter interactions, disrupt trophic levels, and threaten ecosystem stability. Understanding interactions across human land-use gradients is fundamental to mitigating anthropogenic threats effectively and better managing threatened species. Using data from a large-scale camera trap survey, we developed a multispecies occupancy model for a carnivore guild comprising tiger, leopard, and dhole to investigate the effects of environmental (forest and prey abundance) and anthropogenic (settlement) variables on the interspecific interaction. Human settlement density had a strong but contrasting effect on interaction: as settlement density increased, tigers and leopards were less likely to coexist whereas leopards and dholes were more likely to occur together. Tiger and dhole occupancy was negatively associated with settlement density whereas, the leopard was positively associated. Per cent forest cover and large prey abundance had ubiquitous positive effects on carnivore occupancy. Our results indicate that human presence alters available niche space and spatial overlap among predators affecting interactions. The duality in the effect of the settlement on interacting pairs suggests that humans create a landscape of fear for apex predators but promotes coexistence between subordinate species partially supporting the intermediate disturbance hypothesis.
Experimental disturbance treatments of wetland vegetation
<p><em>Study sites</em></p> <p>Our study sites were located in Kastbjerg Ådal (river valley) in Eastern Jutland, Denmark. It is within the Natura 2000 and habitat area no. 223 appointed because of the wide stretch of fens and mires among other qualities. The water course is in good ecological status according to the Water Framework Directive. Nitrogen deposition in this area is low to moderate, 12.5-14.5 kgN/ha/yr (Ellermann et al. 2021). Meadows and fens dominate the study area, known for ‘the longest stretch of rich fen’ in Denmark. Large parts of the river valley are heavily degraded by drainage, fertilization and scrub encroachment, but there have also been recent efforts to restore the watercourse and the valuable rich fens in the valley. Most fens and wet meadows have been abandoned and are now increasingly dominated by tall grasses, tall forbs and willow scrub, but summer grazing occurs in some areas and efforts are made to ensure grazing in the most valuable fens. The drier meadows are typically mown by heavy machinery. The sites were selected to represent gradients in soil moisture from moist to wet and gradients in nutrient status or productivity from poor to rich and included rich fens with characteristic species, fens dominated by <em>Juncus subnodulosus</em> and by <em>Equisetum fluviatile</em>, drained fens encroached by <em>Phragmites australis</em> and natural meadows with characteristic species and encroached by <em>Epilobium hirsutum</em> and meadows characterized by clovers and cultural grasses.</p> <p>The nine sites were of 10 m<sup>2</sup>, each with ten 1 m<sup>2</sup> plots. The 10 plots within each site had treatments assigned randomly. Despite the location in the same river valley, the sites were considered independent because of their different management history and starting conditions and a typical inter-site distance of c. 225 meters. The experiment was established in June 2017 and treatments were repeated monthly during summer and bimonthly during winter, depending on treatment. Responses were recorded in July 2019.</p> <p> </p> <p><em>Experimental set-up and treatments</em></p> <p>Each of the 9 sites were divided into ten 1 m × 1 m plots each with a 0.5 m × 0.5 m inner square and a surrounding plot buffer zone with a control and the following treatments: burning, mowing, trampling, intensive summer grazing (SI), intensive summer grazing with trampling (SIT), extensive summer grazing (SE), extensive summer grazing with trampling (SET, year-round grazing (YR), and year-round grazing with trampling (YRT). Treatments were allocated randomly to each plot with the restriction that the control plot was always in one corner. The experiment was multifactorial with respect to grazing and trampling, whereas burning and mowing were stand-alone treatments. Initial biomass in each plot was estimated at the beginning of the experiment in June 2017 as follows: all standing biomass and litter was removed from the plots by manual cutting at the soil surface and following the micro-topography. Bryophytes were harvested by hand plucking. Biomass, litter and bryophytes from the plot buffer zone were cut separately from the inner square. To estimate the species abundances, a representative sample of the inner square was sorted into litter and live biomass (including bryophytes) by species as sorting the complete biomass was not feasible. All species, litter and biomass from the buffer zone were dried at 55° C and weighed. Using the relative abundance of species in the representative sample and with respect to the weight of the total biomass in the inner square, we estimated the abundance of the species in the inner square.</p> <p>Burning was simulated in March 2018 and 2019. We used wooden boards to shield and adjacent areas were watered before burning the focal plot with a gas weed burner. We burned on a calm day following a dry period with frost to ensure minimum risk of igniting underlying peat and fire spreading over ground, but ensuring that the standing biomass and litter would be dry enough to ignite. This is not a simulation of a naturally occurring wildfire, but corresponds to the conditions that managers would prefer for prescribed conservation burning at larger scales. We simulated mowing as a biomass removal in June 2018. Biomass was removed uniformly across the whole plot in a height of c. 5 cm depending on microtopography. This corresponds to conservation mowing in management but without the added disturbance and pressure from machines. Trampling disturbance was applied using short stilts that could be attached to the field biologist’s boot. The surface of the stilt was 49 cm<sup>2</sup> which corresponds to a pressure of 1.3-1.5 kg/cm<sup>2</sup> with the added weight of the field biologist. This again corresponds to the pressure of a hoof of cattle weighing c. 300-400 kg. Trampling was applied by stepping into the field randomly 60 times once every month from May to September and was the same treatment in combination with intensive, extensive and year round grazing. Grazing was simulated by cutting the above-ground biomass using a 1 m<sup>2</sup> frame divided into a 10 cm coordinate system using the letters A-J on the x-axis and the numbers 1-10 on the y-axis. We cut tufts of biomass within the coordinate system using a list of random combinations of letters and numbers. This system enables “ungrazed” individuals to flower and set seeds. Based on our experience with grazing as an agri-environmental management practice in Denmark, we defined intensive summer grazing as taking place between May and September with the goal of removing all standing biomass by September. Extensive summer grazing also takes place May-September, but we carried this out at half the intensity as intensive summer grazing. Year-round grazing obviously takes place during the whole year (here administered May-September and November, January and March) with the goal of removing all standing biomass by the end of winter (March) before the beginning of a new growing season. We used the initial standing biomass (June 2017) as a measurement of plot productivity and estimated the amount of biomass to be removed during “grazing” as c. 20 % of the initial productivity each month May-September in intensive plots and with all standing biomass “grazed” in September. For extensive plots, we estimated removed biomass as c. 10 % of the initial productivity each month May-September leaving some standing biomass in September. Year-round grazing biomass removal was estimated as c. 10 % of yearly productivity removed every month May-September and November and 20 % removed in January and March resulting in no standing biomass at the end of the winter. As expected plot productivity changed as a result of the treatments, the amount of biomass removed had to be adjusted throughout the experiment. In practice, we aimed for removing twice the amount of biomass in intensive plots relative to extensive plots within the same site and always ensuring that no standing biomass was left in intensive plots in September, c. 50 % of the standing biomass was left in extensive plots in September and no standing biomass was left in year-round grazing plots in March (see actual removed biomass by treatment in Appendix A). All treatments were applied to the whole plot (1 m × 1 m), while the biomass response was only measured in the inner square (0.5 m × 0.5 m), leaving a buffer zone between plots with different treatments.</p> <p> </p> <p><em>Response variables</em></p> <p>A full plot (1 m × 1 m) species list was recorded in the field at the end of the experiment. From this total plot richness, vascular plant plot richness, bryophyte plot richness and number of indicator species per plot were calculated. Indicator species of conservation status are species considered moderately to very sensitive towards habitat degradation as defined by Fredshavn et al. (2010, see Appendix C). Indicator species are often adapted to relatively infertile habitats revealed by low Ellenberg N values and high Grime’s S values reflecting tolerance to nutrient shortage.</p> <p>Mean plot Grime’s C and S values (Grime et al. 1989) were calculated based on vascular plant species lists. We converted Grime’s life strategies to numerical values based on Ejrnæs and Bruun (2000).</p> <p>We performed a Nonmetric Multi-dimensional Scaling analysis (NMDS) on the presence-absence of vascular plant and bryophyte species at the end of the experiment using the function metaMDS in R-package ‘vegan’ (Oksanen et al. 2017) in R version 4.0.3 (R Core Team 2017), using Sørensen dissimilarity and a four-dimensional solution (k =4). The plot coordinates at the three first NMDS axes were extracted (NMS4 was discarded as noise) and these, along with the four richness variables as well as Grime’s C and S values, were used as response variables in Linear Mixed Models (LME) as described in ‘Statistical analyses’.</p> <p>Supplementary to regression models of single response variables we carried out a quadratic discriminant analysis (QDA) as described in ‘Statistical analyses’ using the change in six indicators during the course of the experiment. The difference between plot species richness at the beginning and end of the experiment was calculated based on the species lists from sorted initial biomass and end biomass (0.5 m × 0.5 m). Start-end differences were also calculated separately for vascular plant species richness, bryophyte species richness, richness of indicator species, the ratio between biomass of forbs and graminoids (grasses, sedges and rushes) and Grime’s C and S mean site values.</p> <p> </p> <p><em>Explanatory and co-variables</em></p> <p>Leaf nitrogen, carbon and phosphorous were determined from plot level sampling of leaf plates of grasses, i.e., the most abundant species group across sites. Fresh leaf plates were collected at the beginning and end of the project and then dried, ground and analyzed in the lab. Soil moisture (% volumetric water content) was measured as the mean of four measurements per plot at the beginning and end of the project using a FieldScout TDR 300 Soil Moisture Meter.</p> <p>The total number of species found in each site was used as a co-variable in species richness models reflecting the local species pool.</p> <p> </p> <p><em>Data processing</em></p> <p>All species names were checked for synonyms using the national database arter.dk.</p> <p> </p> <p>References:</p> <p> </p> <p>Ejrnæs, R. and H. H. Bruun (2000). "Gradient analysis of dry grassland vegetation in Denmark." Journal of Vegetation Science <strong>11</strong>(4): 573-584.</p> <p>Ellermann, T., R. Bossi, J. Nygaard, J. H. Christensen, P. Løfstrøm, C. Monies, C. Geels, I. E. Nielsen and M. B. Poulsen (2021). Atmosfærisk deposition 2019. NOVANA. Aarhus, Aarhus Universitet, DCE - Nationalt Center for Miljø og Energi.</p> <p>Fredshavn, J., R. Ejrnæs and B. Nygaard (2010). "Teknisk anvisning for kortlægning af terrestriske naturtyper. TA-N3, Version 1.04. Fagdatacenter for Biodiversitet og Terrestriske Naturdata, Danmarks Miljøundersøgelser. 18 s. ."</p> <p>Grime, J. P., J. G. Hodgson and R. Hunt (1989). Comparative plant ecology: a functional approach to common British species. London, Unwin Hyman.</p> <p>Oksanen, J., F. G. Blanchet, R. Kindt, P. Legendre, R. B. O'Hara, G. L. Simpson, P. Solymos, M. H. H. Stevens and H. Wagner (2017). "Package 'vegan': Community Ecology Package. Version 2.4-3. <a href="http://cran.r-project.org/web/packages/vegan/vegan.pdf">http://cran.r-project.org/web/packages/vegan/vegan.pdf</a>."</p> <p> </p> <p>R Core Team (2017). R: A language and environment for statistical computing. Vienna, Austria, R Foundation for Statistical Computing.</p>
The genetic structure and connectivity in two sympatric rodent species with different life histories are similarly affected by land use disturbances
<p><strong>Microsatellite dataset of the wood mouse (<em>Apodemus sylvaticus)</em> and the bank vole (<em>Myodes glareolus).</em></strong></p> <p>The dataset of the wood mouse is constituted of 194 samples and 7 microsatellite markers: WM_194ind_7STRs.txt</p> <p>The dataset of the bank vole is constituted of 199 samples and 8 microsatellite markers: BV_199ind_8STRs.txt</p> <p>Each locus is encoded in the three-digit format (e.g., 126126) and each column corresponds to a locus specified in the order at the beginning of the file, following the GENEPOP format.</p> <p>Pop indicates the beginning of a new location.</p> <p> </p> <p><em><strong>Locus name in WM_194ind_7STRs.txt</strong></em></p> <p>Locus_1 AS-7-FAM<br> Locus_2 AS-12-PET<br> Locus_3 AS-20-NED<br> Locus_4 AS-34-FAM<br> Locus_5 GTTD9A-PET<br> Locus_6 AS-11-VIC<br> Locus_7 MS-AF-8-NED</p> <p> </p> <p><em><strong>Locus name in BV_199ind_8STRs.txt</strong></em></p> <p>Locus_1 Cg13B8-F_FAM<br> Locus_2 Cg6A1-F_VIC<br> Locus_3 Cg3F12-F_PET<br> Locus_4 Cg13H9-F_PET<br> Locus_5 Cg2E2-F_VIC<br> Locus_6 Cg3E10-F_FAM<br> Locus_7 Cg2A4-F_FAM<br> Locus_8 Cg3A8-F_NED</p>
Data from: Periodic environmental disturbance drives repeated ecomorphological diversification in an adaptive radiation of Antarctic fishes
<p><span>The ecological theory of adaptive radiation has profoundly shaped our conceptualization of the rules that govern diversification. However, while many radiations follow classic early burst patterns of diversification as they fill ecological space, the longer-term fates of these radiations depend on many factors, such as climatic stability. In systems with periodic disturbances, species-rich clades can contain nested adaptive radiations of subclades with their own distinct diversification histories, and how adaptive radiation theory applies in these cases is less clear. Here, we investigated patterns of ecological and phenotypic diversification within two iterative adaptive radiations of cryonotothenioid fishes in Antarctica's Southern Ocean: crocodile icefishes and notoperches. For both clades, we observe evidence of repeated diversification into disparate regions of trait space between closely related taxa and into overlapping regions of trait space between distantly related taxa. We additionally find little evidence that patterns of ecological divergence are correlated with evolution of morphological disparity, suggesting that these axes of divergence may not be tightly linked. Finally, we reveal evidence of repeated convergence in sympatry that suggests niche complementarity. These findings reflect the dynamic history of Antarctic marine habitats, and may guide hypotheses of diversification dynamics in environments characterized by periodic disturbance.</span></p>
Impact of human disturbance on the abundance of non-breeding shorebirds in a subtropical wetland
<p><span>Shorebird populations have declined due to several threats throughout their annual cycle. Anthropogenic disturbance is one of the most ubiquitous threats to shorebird conservation in North America. Here, we studied the influence of human disturbance on shorebird community dynamics during migration and winter in Ensenada de La Paz, a subtropical coastal wetland in Mexico. We used negative binomial generalized linear mixed models to investigate the associations between spatial, biological, and anthropogenic variation and local shorebird abundance that accounted for shorebird body size (small, medium, and large) and foraging strategy (visual and tactile) of 21 shorebird species. After controlling for these different correlates of abundance, human disturbance (people, vehicles, and dogs) was negatively associated with shorebird abundance. During winter, all shorebird species were negatively related to human disturbance but positively associated with presence of raptors. However, small, tactile foraging birds exhibited a proportionally larger negative response to human disturbance than other shorebird types, indicative of guild-level sensitivities to human disturbance regimes. The positive association between shorebird abundance and disturbance from predators was unexpected. Shorebirds likely concentrate in large groups to reduce predation risk, resulting in higher densities of shorebirds occurring in areas with high predation risk. Understanding factors influencing the abundance and habitat use of shorebirds on their non-breeding grounds is paramount to support management and conservation policies for shorebirds and their habitats.</span></p>
Effects of severe anthropogenic disturbance on the heart rate and body temperature in free-living greylag geese (Anser anser)
<p>Anthropogenic disturbances are a major concern for the welfare and conservation of wildlife. We recorded heart rate and body temperature of 20 free-living greylag geese in response to a major regularly re-occurring anthropogenic disturbance, New Year’s Eve fireworks. Heart rate and body temperature were significantly higher in the first and second hour of the new year, compared to the same hour on the 31<sup>st</sup> of December, the average during December and the average during January. Heart rate and body temperature was not significantly affected by sex or age. From 0200-0300 onwards, 1<sup>st</sup> of January heart rates did not significantly differ from the other periods, however body temperatures were significantly increased until 0300-0400. From 0400-0500, heart rate was not affected by any of the investigated factors, whereas body temperature was significantly increased on the 1<sup>st</sup> of January compared 31<sup>st</sup> of December and the December average but not compared to the January average. To conclude, our results show that New Year’s Eve fireworks cause a substantial physiological response, indicative of a stress response in greylag geese, which is costly in terms of energy expenditure.</p>
Low water availability enhances volatile-mediated direct defenses but disturbs indirect defenses against herbivores
<p>1. Interactions between plants and natural enemies of insect herbivores influence plant productivity and survival by reducing herbivory. Plants attract natural enemies via herbivore-induced plant volatiles (HIPVs), but how water availability (WA) influences HIPV-mediated defenses is unclear. </p> <p>2. We use tomato (<em>Solanum lycopersicum</em>), tomato fruitworm (<em>Helicoverpa zea</em>), and two natural enemies, the parasitoid wasp (<em>Microplitis croceipes</em>) and the predator spined soldier bug (<em>Podisus maculiventris</em>), to investigate the effect of WA on HIPV emission dynamics and associated plant defense. </p> <p>3. We show that low WA initially increases total HIPV emission by tomatoes on the first day of herbivore exposure and, in contrast, reduces HIPV emission on the second day. Low WA enhances HIPVs that are mostly found in tomato trichomes. Notably, some volatiles inhibited by low WA are known attractants of natural enemies. Evidence from Y-tube and in-cage behavioral assays indicates that changes in HIPV emissions by low WA compromise the ability of tomato plants to attract natural enemies. </p> <p>4. Synthesis: Based on our results, we propose a hypothesis where plants respond to low WA by enhancing repellent HIPV emissions and reducing the emission of HIPVs that attract natural enemies, which disrupts natural enemy-mediated plant indirect defenses but enhances plant direct defense against herbivores.</p>
Disturbance indicator values for European plants
<p>We report a data set of disturbance indicator values identifying mean optima along gradients of natural and anthropogenic disturbance for 6,382 vascular plant species based on the analysis of 736,366 European vegetation plots and using an expert-based characterization of disturbance regimes in 236 habitat types. The indicator values presented here are crucial for integrating disturbance niche optima in large-scale assessments of vegetation and macroecological studies.</p> <p>The data set contains five main continuous indicator values for European plants: disturbance severity, disturbance frequency, mowing frequency, grazing pressure and soil disturbance. The first two indicators are provided separately for the whole community and the herb layer.</p> <p><strong>Reference:</strong><br> Midolo, G., Herben, T., Axmanová, I., Marcenò, C., Pätsch, R., Bruelheide, H., Karger D.N., Aćić, S., Bergamini, A., Bergmeier, E., Biurrun, I., Bonari, G., Čarni, A., Chiarucci, A., De Sanctis, M., Demina, O., Dengler, J., Dziuba, T., Fanelli, G., Garbolino, E., Giusso del Galdo, G., Goral, F., Güler, B., Hinojos-Mendoza, G., Jansen, F., Jiménez-Alfaro, B., Lengyel, A., Lenoir, J., Pérez-Haase, A., Pielech, R., Prokhorov, V., Rašomavičius, V., Ruprecht, E., Rusina, S., Šilc, U., Škvorc, Ž., Stancic, Z., Tatarenko, I., & Chytrý, M. (2022). Disturbance indicator values for European plants. <em>Global Ecology and Biogeography</em> (Accepted for publication)</p>
Text-fig. 4. a: Conglomeratic to massive sandstone facies 1, facies A are composed of Andesit (AF), Clay (CF) and Sandstone (SF) fragments lain on medium-sandstone. b: Conglomeratic to massive sandstone facies, outcropping of massive sandstone facies comprises of fine to medium grain size of grey to yellowish sandstone. c: Heterolithic sandstone-mudstone facies, intercalation of fine sand with silt and shale as type form of heterolithic sandstone mudstone as indicated by a high sand/shale ratio. d: Example outcrops of heterolithic sandstone-mudstone 2 indicated by low sand/shale ratio. e: Heterolithic fine sand and mudstone and mudstone facies, intercalation of thin sandstone and shale. f: Representative of slump deposits outcrops belong to conglomeratic to massive sandstone facies, which is indicated by the intercalation of sandstone and shale and some disturbed beds or layers as seen in slump deposits. The facies type is normally deposited within the basin floor, channel margin or as a product of the overbank deposits. In this figure the slump deposit is shown as internal bedding, some occurred on the bedding-plane. Trend slope measurement of the fold-axis revealed values N 135°E and N 108°E. in Lithofacies And Ichnofacies Of Turbidite Deposits, West Java, Indonesia
Text-fig. 4. a: Conglomeratic to massive sandstone facies 1, facies A are composed of Andesit (AF), Clay (CF) and Sandstone (SF) fragments lain on medium-sandstone. b: Conglomeratic to massive sandstone facies, outcropping of massive sandstone facies comprises of fine to medium grain size of grey to yellowish sandstone. c: Heterolithic sandstone-mudstone facies, intercalation of fine sand with silt and shale as type form of heterolithic sandstone mudstone as indicated by a high sand/shale ratio. d: Example outcrops of heterolithic sandstone-mudstone 2 indicated by low sand/shale ratio. e: Heterolithic fine sand and mudstone and mudstone facies, intercalation of thin sandstone and shale. f: Representative of slump deposits outcrops belong to conglomeratic to massive sandstone facies, which is indicated by the intercalation of sandstone and shale and some disturbed beds or layers as seen in slump deposits. The facies type is normally deposited within the basin floor, channel margin or as a product of the overbank deposits. In this figure the slump deposit is shown as internal bedding, some occurred on the bedding-plane. Trend slope measurement of the fold-axis revealed values N 135°E and N 108°E.
Data from: Protection status, human disturbance, snow cover and trapping drive density of a declining wolverine population in the Canadian Rocky Mountains
<p>Protected areas are important in species conservation, but high rates of human-caused mortality outside their borders and increasing popularity for recreation can negatively affect wildlife populations. We quantified wolverine (<em>Gulo gulo</em>) population trends from 2011 to 2020 in >14 000 km2 protected and non-protected habitat in southwestern Canada. We conducted wolverine and multi-species surveys using non-invasive DNA and remote camera-based methods. We developed Bayesian integrated models combining spatial capture-recapture data of marked and unmarked individuals with occupancy data. Wolverine density and occupancy declined by 39 percent, with an annual population growth rate of 0.925. Density within protected areas was 3 times higher than outside and declined between 2011 (3.6 wolverines/1000 km2) and 2020 (2.1 wolverines/1000 km2). Wolverine density and detection probability increased with snow cover and decreased near development. Detection probability also decreased with human recreational activity. The annual harvest rate of 13% was above the maximum sustainable rate. We conclude that humans negatively affected the population through direct mortality, sub-lethal effects and habitat impacts. Our study exemplifies the need to monitor population trends for species at risk – within and between protected areas - as steep declines can occur unnoticed if key conservation concerns are not identified and addressed.</p>
Data from: Flying without fear: shooting disturbance has little effect on site preferences in a conflict goose species
<p>Human-modified landscapes have created opportunities for numerous taxa. Agricultural expansion has proven advantageous for several Arctic-breeding goose species, leading to increased abundance and intensified conflict with farmers. Shooting is frequently implemented as a mitigation strategy to control population and via scaring to alter the spatial distribution of conflict species. However, the efficacy of such regimes in manipulating the fear landscape is not always investigated.</p> <p>We developed resource selection functions using GPS-tracking data for Greenland barnacle geese (<em>Branta leucopsis</em>) wintering on Islay, Scotland to assess foraging site choice. We assessed overall foraging site preference and evaluated the influence of shooting management on foraging site selection of key habitats.</p> <p>Barnacle geese selected for improved grassland areas and the likelihood of utilisation varied between these fields according to field-specific management. Protected areas were strongly selected for along with newly reseeded grassland. Field-level exposure to shooting disturbance did not cause a notable change in site selection.</p> <p><strong><em>Synthesis and Applications: </em></strong>Our results demonstrate the importance of providing refuges within managed agricultural landscapes to encourage site use and minimise conflict. We highlight how low intensity shooting disturbance may be ineffective in altering winter habitat selection of high-value foraging sites (especially near roosts). If future management aimed to stimulate redistribution higher intensity shooting disturbance along with the spatial and temporal coordination of shooting effort would likely be required to create a stronger perceived gradient of disturbance risk.</p>
Role of bark beetle disturbance and fuel types on fire radiative power and burn severity in the Bohemian-Saxon Switzerland - Data and Material.
<p>This data repository includes different datasets for fuel types, burn severity, fire radiative power and burned area, which were analysed and used in our paper on the <strong>Role of bark beetle disturbance and fuel types on fire radiative power and burn severity in the Bohemian-Saxon Switzerland</strong>.</p> <p>Study area: National Park Bohemian and Saxon Switzerland and conservation areas, Germany and Czech Republic.</p> <p>Burn severity:<br>dnbr_fire22.nc – Burn severity data covering the burned area, which has been calculated with the Difference Normalized Burn Index (dNBR) using Sentinel-2 and Landsat 8, 9 images. Remote sensing images were reprojected and resampled to 10 m to ensure harmonization before index calculation.</p> <p>cbi.csv – Burn severity surveyed in the field in autumn 2022 as validation data for the dNBR. Contains: ID, coordinates, CBI, CBI values separated for different strata (A to E) and individual strata variables, forest type and species for intermediate trees (strata D) and tall trees (strata E), and the dNBR value that covered the plot extent.</p> <p>Burned area:<br>burned_area.shp – Burned area was mapped by rangers in the Saxon Switzerland National Park and was taken from the dataset provided by the Copernicus Emergency Management Service (EMS) for the Bohemian Switzerland National Park.</p> <p>FRP:<br>frp.nc - Fire Radiative Power gridded to 300 m and clipped to the burned area. FRP during the main fire spread 24/07/22 - 29/07/22. </p> <p>Fuel:<br>fueltype_bohemiansaxonswitzerland.nc/fueltype_bohemiansaxonswitzerland_postfire.nc – Raster datasets (10m spatial resolution, EPSG:32633) of fuels present in the area before and after the fire. The fuel classification system can be found in the fuel_classification.xlsx.</p> <p>fuel_classification.xlsx – The fuel type classification system for the study area. Fuel type ID's as seen in fueltype_bohemiansaxonswitzerland.nc (pre- and postfire).</p>
FIG. 3 in Response of bryophytes to disturbances in managed forests. A case study from a Polish forest
FIG. 3. — Co-correspondence analysis biplot illustrating the ordination of most frequent bryophyte species colonizing ground in relation to the statistically significant environmental variables (n=75). Abbreviations: Age, forest age; DBH.max, maximal trees diameter at breast height; DW.vol, dead wood volume; L, Ellenberg indicator value (EIV) for light; T, EIV for temperature; F, EIV for moisture; R, EIV for pH; N, EIV for nitrogen; the first four letters of species indicate genus name, next four indicate species names and next four letters subspecies names.
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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.