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30 results for “Dominant tree species”
Dalton and Nenana study site data including: invasive plant density estimates, invasive plant density, soil data, seedling estimates for dominant tree species and ground cover estimates for sites
This dataset contains invasive plant and stand level data for study sites along the Dalton and Parks highways in interior Alaska in the summer of 2012. Study sites were situated in burned and mature black spruce forests to compare invasive plant colonization patterns. Invasive plant density estimates along the road adjacent to each site are included, as well as invasive plant density within study sites. Other data includes ground cover estimates for dominant ground cover types, estimates of seedling abundance for dominant tree species, soil paramters (mineral soil pH and mineral soil moisture, residual organic layer/ organic layer depths, and active layer depths).
Figure 3 in Changes in a soil microarthropod community in the vicinity of dominant tree species under trampling management at the Safari Zoological Center, Israel
Figure 3 The taxon richness, Shannon index, Simpson index, and Evenness index (mean ± SD) of soil Acari at different treatment sites at the Safari Zoological Center, Israel, December 2013. OE = open places under enclosure, OT = open places under trampling; EE = E. camaldulensis canopy habitat under enclosure, ET =E. camaldulensis canopy habitat under trampling, TE =T. aphylla canopy habitat under enclosure, TT =T. aphylla canopy habitat under trampling, CE =C. sempervirens canopy habitat under enclosure, CT =C. sempervirens canopy habitat under trampling. Different letters represent significance at p<0.05.
Figure 2 in Changes in a soil microarthropod community in the vicinity of dominant tree species under trampling management at the Safari Zoological Center, Israel
Figure 2 The abundance (individuals per 10 g dry soil substrate; mean ± SD) of soil microarthropod taxa extracted from core samples at different treatment sites at the Safari Zoological Center, Israel, December 2013. OE = open places under enclosure, OT = open places under trampling; EE =E. camaldulensis canopy habitat under enclosure, ET =E. camaldulensis canopy habitat under trampling, TE = T. aphylla canopy habitat under enclosure, TT =T. aphylla canopy habitat under trampling, CE = C. sempervirens canopy habitat under enclosure, CT =C. sempervirens canopy habitat under trampling. Different letters within the same group represent significance at p<0.05.
Figure 1 in Changes in a soil microarthropod community in the vicinity of dominant tree species under trampling management at the Safari Zoological Center, Israel
Figure 1 Location of study sites at the Safari Zoological Center, Israel. OE = open places under enclosure, OT = open places under trampling; EE =E. camaldulensis canopy habitat under enclosure, ET = E. camaldulensis canopy habitat under trampling, TE =T. aphylla canopy habitat under enclosure, TT = T. aphylla canopy habitat under trampling, CE =C. sempervirens canopy habitat under enclosure, CT = C. sempervirens canopy habitat under trampling.
Data for: Genomic vulnerability to climate change in Quercus acutissima, a dominant tree species in East Asian deciduous forests
<p><span>Understanding the evolutionary processes that shape the landscape of genetic variation and influence the response of species to future climate change is critical for biodiversity conservation. Here, we sampled </span><span>27</span><span> populations across the distribution range of a dominant forest tree, <em>Quercus</em> <em>acutissima</em>, in East Asia, and applied genome-wide analyses to track the evolutionary history and predict the fate of populations under future climate. We found two genetic groups (East and West) in <em>Q</em>. <em>acutissima</em> that diverged during the Pliocene. </span><span>We also found</span><span> a heterogeneous landscape of genomic variation in this species</span><span>, which may have been shaped by </span><span>population demography and </span><span>linked selections</span><span>.</span><span> Using genotype-environment association analyses, we identified climate-associated SNPs in a diverse set of genes and functional categories, indicating a model of polygenic adaptation in <em>Q</em>. acutissima<em>.</em> We further estimated three genetic offset metrics to quantify genomic vulnerability of this species to climate change due to the complex interplay </span><span>between</span><span> local adaptation</span><span> and</span><span> migration</span><span>.</span><span> We found that marginal populations are under </span><span>higher</span><span> risk of local extinction</span><span> because of</span><span> future climate change</span><span>, and may not be able to track </span><span>suitable habitats </span><span>to maintain the gene-environment relationships observed under the current climate.</span><span> We also detected higher reverse genetic offsets in northern China, indicating that genetic variation currently present in the whole range of <em>Q</em>. <em>acutissima</em> may not adapt to future climate conditions in this area.</span> <span>Overall, this study</span><span> illustrates how evolutionary</span><span> processes </span><span>have</span><span> shaped the landscape of genomic variation, and</span><span> provides a comprehensive genome-wide view of climate maladaptation in <em>Q</em>. <em>acutissima</em>.</span></p>
Data for: Genomic vulnerability to climate change in Quercus acutissima, a dominant tree species in East Asian deciduous forests
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Table 2 in Changes in a soil microarthropod community in the vicinity of dominant tree species under trampling management at the Safari Zoological Center, Israel
<p><b>Table 2</b> Mean values (± SD) of soil physical and chemical parameters at different treatment sites at the Safari Zoological Center, Israel, December 2013. SM = soil moisture, OM = organic matter, pH = soil pH, SEC = soil electrical conductivity, SD = soil density, WHC = water-holding capacity. OE = open places under enclosure conditions, OT = open places under trampling conditions; EE <i>E.</i> = <i>camaldulensis</i> canopy habitat under enclosure conditions, ET = <i>E</i>. <i>camaldulensis</i> canopy habitat under trampling conditions, TE <i>T</i> =. <i>aphylla</i> canopy habitat under enclosure conditions, TT = <i>T. aphylla</i> canopy habitat under trampling conditions, CE = <i>C</i>. <i>sempervirens</i> canopy habitat under enclosure conditions, CT = <i>C. sempervirens</i> canopy habitat under trampling conditions. Different letters in the same column represent significant difference <i>p</i> at <0.05.</p><table><tbody><tr><th></th><th>SM (%)</th><th>OM (%)</th><th>pH</th><th>SEC (µ -1) cm</th><th>SD (g -3) cm</th><th>WHC (%)</th></tr></tbody><tbody><tr><th>OE</th><td>25.6±3.4a</td><td>1.1±0.2b</td><td>7.5±0.2b</td><td>87.6±17.5d</td><td>1.1±0.0b</td><td>53.6±0.9ab</td></tr><tr><th>OT</th><td>7.8±1.7c</td><td>0.2±0.0e</td><td>7.6±0.0b</td><td>150.3±51.3c</td><td>1.6±0.0a</td><td>25.6±1.0c</td></tr><tr><th>EE</th><td>16.6±1.6b</td><td>1.3±0.2b</td><td>7.6±0.0b</td><td>130.2±9.4cd</td><td>1.0±0.1c</td><td>52.6±11.1ab</td></tr><tr><th>ET</th><td>23.2±3.8a</td><td>2.0±0.3a</td><td>7.6±0.0b</td><td>255.3±39.6ab</td><td>1.1±0.0bc</td><td>31.9±3.5c</td></tr><tr><th>TE</th><td>21.9±4.4ab</td><td>0.4±0.1d</td><td>7.9±0.0a</td><td>152.0±17.8c</td><td>1.0±0.1c</td><td>52.1±14.6ab</td></tr><tr><th>TT</th><td>14.1±5.2b</td><td>1.1±0.1b</td><td>7.6±0.1b</td><td>254.1±48.0ab</td><td>1.0±0.1c</td><td>43.3±6.2b</td></tr><tr><th>CE</th><td>26.9±3.4a</td><td>0.8±0.3c</td><td>7.6±0.1b</td><td>209.9±22.5b</td><td>1.0±0.1c</td><td>56.3±5.8a</td></tr><tr><th>CT</th><td>22.0±6.0ab</td><td>0.5±0.2d</td><td>7.8±0.1a</td><td>275.9±21.9a</td><td>1.0±0.0c</td><td>43.0±3.9b</td></tr></tbody></table>
Table 3 in Changes in a soil microarthropod community in the vicinity of dominant tree species under trampling management at the Safari Zoological Center, Israel
<p><b>Table 3</b> Effects of sampling habitat (“Habitat”), trampling management (“Trampling”), and their interaction on soil parameters, abundance of soil microarthropods, and diversity indices of soil Acari at the Safari Zoological Center, Israel, December 2013 (General linear model, α = 0.05). * <i>p</i> <0.05, ** <i>p</i> <0.01, *** <i>p</i> <0.001.</p><table><tbody><tr><th><b>Microarthropods</b></th><th><i>d</i> <i>f</i></th><th><i>F</i></th><th><b>Soil parameters</b></th><th><i>d</i> <i>f</i></th><th><i>F</i></th></tr></tbody><tbody><tr><th><b>Total microarthropod abundance</b></th><td></td><td></td><td><b>Soil moisture</b></td><td></td><td></td></tr><tr><th>Model</th><td>8</td><td>15.85***</td><td>Model</td><td>8</td><td>109.38***</td></tr><tr><th>Trampling</th><td>1</td><td>39.13***</td><td>Trampling</td><td>1</td><td>18.46***</td></tr><tr><th>Habitat</th><td>3</td><td>1.65</td><td>Habitat</td><td>3</td><td>5.90**</td></tr><tr><th>Trampling * Habitat</th><td>3</td><td>4.89**</td><td>Trampling * Habitat</td><td>3</td><td>12.84***</td></tr><tr><th><b>Collembola abundance</b></th><td></td><td></td><td><b>Organic matter</b></td><td></td><td></td></tr><tr><th>Model</th><td>8</td><td>4.90**</td><td>Model</td><td>8</td><td>116.32***</td></tr><tr><th>Trampling</th><td>1</td><td>11.18**</td><td>Trampling</td><td>1</td><td>0.05</td></tr><tr><th>Habitat</th><td>3</td><td>2.29</td><td>Habitat</td><td>3</td><td>48.99***</td></tr><tr><th>Trampling * Habitat</th><td>3</td><td>2.56</td><td>Trampling * Habitat</td><td>3</td><td>32.99***</td></tr><tr><th><b>Other arthropod abundance</b></th><td></td><td></td><td><b>Soil pH</b></td><td></td><td></td></tr><tr><th>Model</th><td>8</td><td>1</td><td>Model</td><td>8</td><td>35120.21***</td></tr><tr><th>Trampling</th><td>1</td><td>1.8</td><td>Trampling</td><td>1</td><td>0.5</td></tr><tr><th>Habitat</th><td>3</td><td>0.73</td><td>Habitat</td><td>3</td><td>4.69*</td></tr><tr><th>Trampling * Habitat</th><td>3</td><td>0.73</td><td>Trampling * Habitat</td><td>3</td><td>13.93***</td></tr><tr><th><b>Soil Acari abundance</b></th><td></td><td></td><td><b>Electrical conductivity</b></td><td></td><td></td></tr><tr><th>Model</th><td>8</td><td>18.85***</td><td>Model</td><td>8</td><td>156.31***</td></tr><tr><th>Trampling</th><td>1</td><td>43.09***</td><td>Trampling</td><td>1</td><td>61.80***</td></tr><tr><th>Habitat</th><td>3</td><td>0.88</td><td>Habitat</td><td>3</td><td>20.89***</td></tr><tr><th>Trampling * Habitat</th><td>3</td><td>3.60*</td><td>Trampling * Habitat</td><td>3</td><td>1.76</td></tr><tr><th><b>Taxon richness of soil Acari</b></th><td></td><td></td><td><b>Soil density</b></td><td></td><td></td></tr><tr><th>Model</th><td>8</td><td>16.11***</td><td>Model</td><td>8</td><td>1769.86***</td></tr><tr><th>Trampling</th><td>1</td><td>34.68***</td><td>Trampling</td><td>1</td><td>57.12***</td></tr><tr><th>Habitat</th><td>3</td><td>3.17*</td><td>Habitat</td><td>3</td><td>82.99***</td></tr><tr><th>Trampling * Habitat</th><td>3</td><td>1.23</td><td>Trampling * Habitat</td><td>3</td><td>36.99***</td></tr><tr><th><b>Shannon index of soil Acari</b></th><td></td><td></td><td><b>Water-holding capacity</b></td><td></td><td></td></tr><tr><th>Model</th><td>8</td><td>18.88***</td><td>Model</td><td>8</td><td>155.49***</td></tr><tr><th>Trampling</th><td>1</td><td>51.07***</td><td>Trampling</td><td>1</td><td>45.98***</td></tr><tr><th>Habitat</th><td>3</td><td>4.03*</td><td>Habitat</td><td>3</td><td>3.22*</td></tr><tr><th>Trampling * Habitat</th><td>3</td><td>0.78</td><td>Trampling * Habitat</td><td>3</td><td>2.6</td></tr><tr><th><b>Simpson index of soil Acari</b></th></tr><tr><th>Model</th><td>8</td><td>13.42***</td><td></td><td></td><td></td></tr><tr><th>Trampling</th><td>1</td><td>0</td><td></td><td></td><td></td></tr><tr><th>Habitat</th><td>3</td><td>7.47**</td><td></td><td></td><td></td></tr><tr><th>Trampling * Habitat</th><td>3</td><td>5.22**</td><td></td><td></td><td></td></tr><tr><th><b>Evenness index of soil Acari</b></th></tr><tr><th>Model</th><td>8</td><td>42.11***</td><td></td><td></td><td></td></tr><tr><th>Trampling</th><td>1</td><td>120.61***</td><td></td><td></td><td></td></tr><tr><th>Habitat</th><td>3</td><td>3.68*</td><td></td><td></td><td></td></tr><tr><th>Trampling * Habitat</th><td>3</td><td>1.82</td><td></td><td></td><td></td></tr></tbody></table>
Table 1 in Changes in a soil microarthropod community in the vicinity of dominant tree species under trampling management at the Safari Zoological Center, Israel
<p><b>Table 1</b> Sampling design (replication = 4) for sites at the Safari Zoological Center, Israel, December 2013. Herbaceous ground cover: +++ patchy; + a few plants, – no plants. OE = open places under enclosure conditions, OT = open places under trampling conditions; EE <i>E</i> =. <i>camaldulensis</i> canopy habitat under enclosure conditions, ET = <i>E. camaldulensis</i> canopy habitat under trampling conditions, TE <i>T</i> =. aphylla canopy habitat under enclosure conditions, TT <i>T</i> =. <i>aphylla</i> canopy habitat under trampling conditions, CE = <i>C</i>. <i>sempervirens</i> canopy habitat under enclosure conditions, CT = <i>C</i>. <i>sempervirens</i> canopy habitat under trampling conditions.</p><table><tbody><tr><th>Habitat</th><th>Code</th><th>Treatment</th><th>Tree height (m)</th><th>Tree canopy crown (m2)</th><th>Herbaceous vegetation</th><th>Soil physical/biological top layer</th><th>Litter layer (cm)</th></tr></tbody><tbody><tr><th>Open spaces</th><td>OT OE</td><td>Trampling Enclosure</td><td>- -</td><td>- -</td><td>No +++</td><td>No Physical top layer</td><td>No No</td></tr><tr><th><i>E. camaldulensis</i></th><td>ET EE</td><td>Trampling Enclosure</td><td>10-13</td><td>6×8</td><td>No +</td><td>No Biological top layer</td><td>No 2-3</td></tr><tr><th><i>T. aphylla</i></th><td>TT TE</td><td>Trampling Enclosure</td><td>14-16</td><td>8×8</td><td>No +++</td><td>No Physical top layer</td><td>No Few</td></tr><tr><th><i>C. sempervirens</i></th><td>CT CE</td><td>Trampling Enclosure</td><td>14-16</td><td>7×9</td><td>No +</td><td>No Biological layer</td><td>No 1-2</td></tr></tbody></table>
Table 4 in Changes in a soil microarthropod community in the vicinity of dominant tree species under trampling management at the Safari Zoological Center, Israel
<p><b>Table 4</b> Correlation coefficients (Pearson correlation, <i>r</i>) between the abundance of microarthropods, diversity indices of soil Acari, and soil parameters at the Safari Zoological Center, Israel, December 2013. SM = soil moisture, OM = organic matter, pH = soil pH, SEC = soil electrical conductivity, SD = soil density, WHC = water-holding capacity <i>p</i>. <*0.05, ** <i>p</i> <0.01, *** <i>p</i> <0.001.</p><table><tbody><tr><th><b>Index</b></th><th></th><th><b>SM</b></th><th><b>OM</b></th><th><b>pH</b></th><th><b>SEC</b></th><th><b>SD</b></th><th><b>WHC</b></th></tr></tbody><tbody><tr><th></th><td>Acari</td><td>0.349*</td><td>0.068</td><td>-0.198</td><td>-0.506**</td><td>-0.299</td><td>0.571***</td></tr><tr><th>Abundance</th><td>Collembola Other soil arthropods</td><td>0.153 0.202</td><td>0.210 0.098</td><td>-0.486** -0.294</td><td>-0.506** -0.209</td><td>-0.107 -0.065</td><td>0.207 0.245</td></tr><tr><th></th><td>Total microarthropod</td><td>0.292</td><td>0.158</td><td>-0.403*</td><td>-0.574***</td><td>-0.233</td><td>0.445*</td></tr><tr><th>Diversity indices of Acari</th><td>Taxon richness Shannon index Simpson index</td><td>0.253 0.285 -0.006</td><td>0.023 0.032 -0.175</td><td>-0.098 -0.120 0.165</td><td>-0.392* -0.455** 0.240</td><td>-0.316 -0.293 -0.475**</td><td>0.561*** 0.585*** 0.336</td></tr><tr><th></th><td>Evenness index</td><td>0.387*</td><td>0.009</td><td>-0.203</td><td>-0.466**</td><td>-0.411*</td><td>0.739***</td></tr></tbody></table>
Integrated effects of neighborhood composition and resource levels on growth of a dominant tree species in a tropical forest
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Data from: The frequency, magnitude, and spatial distribution of heart rot in dominant temperate tree species in a forest dynamics plot
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Mycorrhizal dominance influences tree species richness and richness-biomass relationship in China’s forests
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Divergent responses of forest dominant trees species to the manipulated canopy and understory nitrogen additions in terms of foliage stoichiometric, economic and hydraulic traits
<p>Nitrogen (N) deposition effects on the stoichiometric balance and photosynthetic and hydraulic couplings in subtropical forests has drawn wide attentions. The previously adopted understory application of N fertilization is criticized because it might ignore foliar N retention for different species. This paper reports a fertilizing application from the canopy (CAN) and under the canopy (UAN) in a phosphorus (P) limited ecosystem. Foliage stoichiometric, photosynthetic and hydraulic traits of six dominant species were measured and analyzed. Both treatments equally enhanced foliage N and N/P, but not foliage P, who was highly species-specific depending on tree height, which implied enhanced P limitation. Decreased isotope abundance of <sup><span>15</span></sup>N (δ<sup><span>15</span></sup>N) that approaching to the level in the urea fertilizer under CAN suggested the existence of canopy retention of N. Besides, N response sensitivity of N, P and δ<sup><span>15</span></sup>N that positively related to tree height (H) under CAN indicated different exposure to the added N, which promoted stoichiometric imbalance among species. The photosynthetic traits represented by net photosynthesis (<i><span>A</span></i><sub><span>n</span></sub>) increased under both treatments. A divergent foliar photosynthetic and hydraulic traits varations was identified by signifcant decreased stomatal conductance (<i>g</i><sub><span>s</span></sub>) and <i><span>A</span></i><sub><span>n </span></sub>/<i><span>g</span></i><sub><span>s</span></sub> for CAN treatments, which induced the elevated isotope abundance of <sup><span>13</span></sup>C (δ<sup><span>13</span></sup>C). Correspondingly, foliage hydraulic traits that shifted to water use efficiency axis were identified only under CAN in principal component analysis. Overall, our results proved that the canopy obsorbtion and species heterogeneity should be considered regarding foliar safety vs efficiency trade-off in response to nitrogen additions in the future.</p>
Data from: Variations in ratio and loads of soil nitrogen and phosphorus explain the coexistence of dominant tree species in a boreal forest of Xinjiang, northwest China
<p><span>The resource ratio hypothesis (RRH) and the nutrient-load hypothesis (NLH) state that species coexistence is driven by the ratios and loads (contents) of multiple limiting resources, respectively. However, roles of resource ratios and loads to mature forest ecosystems remains unclear. Data were collected within 300 quadrats (20m×20m) spread across a 12 ha plot of boreal forest in the Kanas of Xinjiang, northwest China. We used torus translation tests to analyze the associations of dominant tree species with specific microhabitats. The linear mixed models were used to assess effects of resource ratios and contents on abundance and basal area of specific species, as well as within different life stages. Two shade-tolerant species, <i>Picea obovata</i> and <i>Pinus sibirica</i>, exhibited opposite relationships to the spatial distribution of soil nitrogen (N) content and phosphorus (P) content. <i>Picea. obovata</i> was associated with microhabitats with high N:P ratio, while <i>P. sibirica</i> preferred microhabitats with low N:P ratio. The light-demanding trees, <i>Betula pendula</i> clustered at both low N and P sites. Another light-demanding trees, <i>Larix sibirica</i>, did not show any significant habitat preferences. Moreover, N:P ratio mainly affected species abundance, while their contents largely impacted basal area of species. And effects of N:P ratio or contents on species distribution showed a decreasing trend from sapling to adults. Overall, our findings indicate that niche partitioning caused by resource variations may alleviate interspecific competition and contribute to the species coexistence, providing convincing proof for the importance of resource ratio and load on maintaining diversity in boreal forests. </span></p>
Variations in leaf economics spectrum traits for an evergreen coniferous species: Tree size dominates over environment factors
<ol> <li>Many leaf traits strongly vary with tree size and environmental factors, but the importance of these factors to intraspecific variations of leaf traits in forest trees have rarely been <a><span>simultaneously</span></a> evaluated.</li> <li>We measured needle longevity and specific leaf area (SLA) and nitrogen (N) content of every needle age (0 to 4 year old) for 65 individuals with 0.3-100 cm diameter at breast height (DBH) for an evergreen coniferous species, <i>Pinus koraiensis</i> Sieb. et Zucc., in Northeast China. We <a><span>simultaneously</span></a> evaluated effects of tree size (DBH or tree height) and environment factors (light intensity, soil N content and water availability) on the needle longevity, SLA, foliage N content as well as the slopes of regressions of SLA and foliage N content against needle age.</li> <li>All of the studied leaf traits and slopes of regressions of SLA and foliage N content against needle age were significantly related to tree size. Tree height had a greater impact on SLA and area-based leaf N content (N<sub>area</sub>), whereas DBH was more important for needle longevity and mass-based leaf N content (N<sub>mass</sub>). The environment variables, light intensity, soil N content and water availability, were rather minor factors for trait variations compared with tree size. Significant influences of light intensity were found only on needle longevity, and soil N and water availability had no effects on the leaf traits.</li> <li>Our study clearly showed that tree size is an important driver of intraspecific variations in the key leaf traits of <i>Pinus koraiensis</i> in a natural forest. We also emphasize the importance of DBH or tree height varies depending on leaf traits, suggesting various mechanisms of size effects on the intraspecific variations in leaf traits. We suggest that ecological significance of leaf trait variations needs reconsideration incorporating tree size effect.</li> </ol>
Data from: AFLP diversity and spatial structure of Calycophyllum candidissimum (Rubiaceae), a dominant tree species of Nicaragua's critically endangered seasonally dry forest
The Central American seasonally dry tropical (SDT) forest biome is one of the worlds' most endangered ecosystems, yet little is known about the genetic consequences of its recent fragmentation. A prominent constituent of this biome is Calycophyllum candidissimum, an insect-pollinated and wind-dispersed canopy tree of high socio-economic importance, particularly in Nicaragua. Here, we surveyed amplified fragment length polymorphisms across 13 populations of this species in Nicaragua to elucidate the relative roles of contemporary vs historical factors in shaping its genetic variation. Genetic diversity was low in all investigated populations (mean HE=0.125), and negatively correlated with latitude. Overall population differentiation was moderate (ΦST=0.109, P<0.001), and Bayesian analysis of population structure revealed two major latitudinal clusters (I: 'Pacific North'+'Central Highland'; II: 'Pacific South'), along with a genetic cline between I and II. Population-based cluster analyses indicated a strong pattern of 'isolation by distance' as confirmed by Mantel's test. Our results suggest that (1) the low genetic diversity of these populations reflects biogeographic/population history (colonisation from South America, Pleistocene range contractions) rather than recent human impact; whereas (2) the underlying process of their isolation by distance pattern, which is best explained by 'isolation by dispersal limitation', implies contemporary gene flow between neighbouring populations as likely facilitated by the species' efficient seed dispersal capacity. Overall, these results underscore that even tree species from highly decimated forest regions may be genetically resilient to habitat fragmentation due to species-typical dispersal characteristics, the necessity of broad-scale measures for their conservation notwithstanding.
Data from: Fungal communities influence decomposition rates of plant litter from two dominant trees species
The home-field advantage hypothesis (HFA) predicts that plant litter decomposes faster than expected underneath the plant from which it originates. We tested this hypothesis in a decomposition experiment where litters were incubated reciprocally in neighbouring European beech and Norway spruce forests. We analysed fungal communities in the litter through DNA metabarcoding and evaluated the effect of mesofauna (mites and springtails) on litter mass loss by using different litter-bag mesh sizes. Accounting for general differences in decomposition between litter and forest types, we found a significant home field advantage of 24%. Litter decomposed faster in the beech forest but spruce litter decomposed faster than beech litter. Fungal communities showed a clear dependency on both forest and litter type. Mesofauna did not affect litter mass loss rates or microbial species composition.
Tradeoffs between leaf cooling and hydraulic safety in a dominant arid land riparian tree species
<p>Leaf carbon gain optimization in hot environments requires balancing leaf thermoregulation with avoiding excessive water loss via transpiration and hydraulic failure. The tradeoffs between leaf thermoregulation and transpirational water loss can determine the ecological consequences of heat waves that are increasing in frequency and intensity. We evaluated leaf thermoregulation strategies in warm (>40 °C maximum summer temperature) and cool-adapted (<40 °C maximum summer temperature) genotypes of the foundation tree species, <em>Populus fremontii</em> using a common garden near the mid-elevational point of its distribution. We measured leaf temperatures and assessed three modes of leaf thermoregulation: leaf morphology, midday canopy stomatal conductance, and stomatal sensitivity to vapor pressure deficit. Data were used to parameterize a leaf energy balance model to estimate contrasts in midday leaf temperature in warm- and cool-adapted genotypes. Warm-adapted genotypes had 39% smaller leaves and 38% higher midday stomatal conductance, reflecting a 3.8 °C cooler mean leaf temperature than cool adapted genotypes. Leaf temperatures modeled over the warmest months were on average 1.1 °C cooler in warm- relative to cool-adapted genotypes. Results show that plants adapted to warm environments are predisposed to tightly regulate leaf temperatures during heat waves, potentially at an increased risk of hydraulic failure. </p>
Data from: Long-term and interactive effects of different mammalian consumers on growth, survival and recruitment of dominant tree species
<p>Throughout the world, numerous tree species are reported to be in decline, either due to increased mortality of established trees or reduced recruitment. The situation appears especially acute for oaks, which are dominant features of many landscapes in the northern hemisphere. Although numerous factors have been hypothesized to explain reductions in tree performance, vertebrate herbivores and granivores may serve as important drivers of these changes. Here, using data from 8- and 14-year-old exclosure experiments, we evaluated the individual and interactive effects of large and small mammalian herbivores on the performance of three widespread oak species in California – coast live oak (<i>Quercus agrifolia</i>), California black oak (<i>Q. kelloggii</i>) and Oregon white oak (<i>Q. garryana</i>). Although impacts varied somewhat by species and experiment, herbivory by black-tailed deer (<i>Odocoileus hemionus columbianus</i>) reduced the height and survival of juvenile coast live oaks and altered their architecture, as well as reduced the abundance of black oak seedlings, the richness of woody species and the cover of non-oak woody species. Small mammals (<i>Microtus californicus</i> and <i>Peromyscus maniculatus</i>) had even more widespread effects, reducing the abundance of black oak seedlings and the height and cover of all three oak species. We also detected numerous interactions between small mammals and deer, with one herbivore having positive or negative effects on oak abundance and cover when the other herbivore was either present or absent. For example, deer often had negative effects on seedling abundance only when, or even more so when, small mammals were present. In summary, mammalian consumers play crucial roles in limiting oak recruitment by reducing seedling abundance, maintaining trees in stunted states and preventing them from reaching sapling stages and becoming reproductive. Interactions between large and small mammals can also alter the intensity and direction of their effects on trees.</p>
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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.