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58 results for “Alpine grasslands”
CO2 NEE and ER + air and soil meteorological and climate parameters in Alpine grasslands, Gran Paradiso National Park, 2017-2019
<p>The dataset “fluxes_meteoclimate_nivolet_V0” is a .csv file reporting CO<sub>2</sub> Net Ecosystem Exchange (NEE) and Ecosystem Respiration (ER) measured at Nivolet Plain, Gran Paradiso National Park, Italy, in a high-altitude Alpine grassland environment (about 2700 m.a.s.l.) using the flux chamber method, during the 2017, 2018 and 2019 vegetative seasons (July-September), approximately twice a month. NEE is measured with a transparent flux chamber, while ER with a shaded chamber. Data represent the average values and the corresponding standard deviations obtained from four sites at different altitudes and geological substrate of the soil. Each average value is obtained as a mean over a set of more than 20 point-measures for each site and each sampling date. Flux data are complemented by measurements of soil temperature and volumetric water content, air temperature and moisture, and solar radiance. The four sites are characterized by soils developed over carbonates (carb) (45.500212N-7.152213E), glacial deposits (glac) (45.490167N-7.139916E), gneiss rocks (gnei) (45.490256N-7.149253E) and alluvial deposits (allu) (45.492656 N-7.146092 E).</p> <p>Other relevant shortcuts used in the .csv table: Std = Standard deviation; VWC% = Volumetric Water Content %. Meteorological and climate variables recorded during the measurement of NEE and during the measurement of ER bring the suffix NEE and ER respectively (es. Pressure_NEE (hPa) = atmospheric pressure recorded during the measurement of Net Ecosystem Exchange).</p>
Net Ecosystem Exchange, Ecosystem Respiration and meteoclimatic data of Alpine grasslands at Nivolet Plain, Gran Paradiso National Park, Italy 2017-2023
<p>This dataset presents georeferenced measurements collected at the Nivolet Plain in Gran Paradiso National Park (GPNP), western Italian Alps. The dataset includes the Net Ecosystem Exchange (NEE), Ecosystem Respiration (ER) and meteo-climatic variables, i.e. air and soil temperature, air relative humidity, soil volumetric water content, atmospheric pressure and solar irradiance. The measurements were conducted between 2017 and 2023 at five different sites at an elevation of approximately 2550-2750 meters a.s.l.</p> <p>To estimate NEE and ER, we employed the flux chamber method, measuring the temporal variation of carbon dioxide (CO2) concentration inside the chamber over a period of about 90 seconds. We used a customized portable non-steady-state dynamic flux chamber, paired with an InfraRed Gas Analyzer (IRGA) and a portable weather station. Measurements were taken at around 20 points per site during the snow-free season, spanning from June to October.</p> <p>The dataset is provided in a comma-separated text file (.csv) format. Each record corresponds to a single measurement point, with semicolons used as separators. The "NA" notation indicates values that are not available or have been excluded during quality control processes (e.g., due to battery failure). We use point as decimal separator.</p> <p>The sign convention for the fluxes is: a negative value indicates a CO2 flux from the atmosphere to the ecosystem, while a positive value represents a CO2 flux from the soil/ecosystem to the atmosphere. Consequently, ER values are positive, while NEE values can be positive or negative. The units for NEE and ER fluxes are molCO2 m-2 day-1 and μmolCO2 m-2 second-1. The first values in each record of the dataset indicate the observation details (sampling date, site, etc.), followed by the corresponding measured or calculated variables. NEE and ER values were estimated from the slope of the linear regression of CO2 concentration over time (ppm s-1) using a laboratory calibration curve.</p> <p>The calibration curve was created by relating known and pre-set CO2 fluxes (within the range expected in the field) with the corresponding measured slopes. The flux values were then scaled up based on the area of the chamber base (0.036 m2) and adjusted using the ratio of atmospheric pressure and air temperature during the measurement to those recorded during the calibration in the laboratory.</p>
Indicative distribution map for Ecosystem Functional Group T6.5 Tropical alpine grasslands and herbfields
<p>This archive contains indicative distribution maps and profiles for <strong>T6.5 Tropical alpine grasslands and herbfields</strong>, a ecosystem functional group (EFG, level 3) of the <a href="https://global-ecosystems.org/">IUCN Global Ecosystem Typology</a> (v2.0). Please refer to Keith <em>et al.</em> (2020) for details.</p> <p>The descriptive profiles provide brief summaries of key ecological traits and processes, maps are indicative of global distribution patterns, and are not intended to represent fine-scale patterns. The maps show areas of the world containing major (value of 1, coloured red) or minor occurrences (value of 2, coloured yellow) of each ecosystem functional group. Minor occurrences are areas where an ecosystem functional group is scattered in patches within matrices of other ecosystem functional groups or where they occur in substantial areas, but only within a segment of a larger region. Given bounds of resolution and accuracy of source data, the maps should be used to query which EFG are likely to occur within areas, rather than which occur at particular point locations. Detailed methods and references for the maps are included in the profile (xml format).</p>
Indicative distribution map for Ecosystem Functional Group T6.4 Temperate alpine grasslands and shrublands
<p>This archive contains indicative distribution maps and profiles for <strong>T6.4 Temperate alpine grasslands and shrublands</strong>, a ecosystem functional group (EFG, level 3) of the <a href="https://global-ecosystems.org/">IUCN Global Ecosystem Typology</a> (v2.0). Please refer to Keith <em>et al.</em> (2020) for details.</p> <p>The descriptive profiles provide brief summaries of key ecological traits and processes, maps are indicative of global distribution patterns, and are not intended to represent fine-scale patterns. The maps show areas of the world containing major (value of 1, coloured red) or minor occurrences (value of 2, coloured yellow) of each ecosystem functional group. Minor occurrences are areas where an ecosystem functional group is scattered in patches within matrices of other ecosystem functional groups or where they occur in substantial areas, but only within a segment of a larger region. Given bounds of resolution and accuracy of source data, the maps should be used to query which EFG are likely to occur within areas, rather than which occur at particular point locations. Detailed methods and references for the maps are included in the profile (xml format).</p>
CO2 Net Ecosystem Exchange (NEE) and Ecosystem Respiration (ER) + meteorological parameters in alpine grasslands at Nivolet Plain, Gran Paradiso National Park, 2020 (IGG-CNR-CZO@NIVOLET)
<p>CO2 Net Ecosystem Exchange (NEE) and Ecosystem Respiration (ER) measured at Nivolet Plain, Gran Paradiso National Park, Italy, in a high-altitude Alpine grassland environment (about 2500-2700 m.a.s.l.) using the closed portable flux chamber method during the 2020 vegetative season (July-October), approximately twice a month. NEE is measured with a transparent chamber, while ER with a dark chamber (transparent chamber shaded with a cloth). Data represent the average values and the corresponding standard deviations obtained from five sites at different altitudes and soil substrates. Each average value is obtained as a mean over a set of 20 point-measurements for each site and each sampling date. Flux data are complemented by measurements of soil temperature and soil volumetric water content, air temperature, air RH, and solar radiance.</p> <p>During the measurement, air is pumped from the chamber to an IR gas analyzer (IRGA) and then injected again in the chamber. The CO2 concentration inside the chamber is measured for about 90 seconds and then the rate of concentration change is linearly interpolated (over 60s) to obtain the flux measurements. A detailed description of the sampling method can be found in Magnani et al. (2020).</p> <p>Instrumentation used: accumulation chambers (height: 31.5 cm; area of the base: 363 cm2), LI-COR LI-840 & LI-850 IR spectrophotometers, stainless-steel collars (inserted into the soil to a depth of about 1 cm), portable meteorological stations (pyranometer LSI Lastem DPA053, thermohygrometer LSI Lastem DMA672.1), pt100 soil temperature sensors, SM150T soil moisture sensor.</p>
CO2 Net Ecosystem Exchange (NEE) and Ecosystem Respiration (ER) + meteorological parameters in alpine grasslands at Nivolet Plain, Gran Paradiso National Park, 2021 (IGG-CNR-CZO@NIVOLET)
<p>CO2 Net Ecosystem Exchange (NEE) and Ecosystem Respiration (ER) measured at Nivolet Plain, Gran Paradiso National Park, Italy, in a high-altitude Alpine grassland environment (about 2500-2700 m.a.s.l.) using the closed portable flux chamber method during the 2021 vegetative season (July-October), approximately twice a month. NEE is measured with a transparent chamber, while ER with a dark chamber (transparent chamber shaded with a cloth). Data represent the average values and the corresponding standard deviations obtained from five sites at different altitudes and soil substrates. Each average value is obtained as a mean over a set of 20 point-measurements for each site and each sampling date. Flux data are complemented by measurements of soil temperature and soil volumetric water content, air temperature, air RH, and solar radiance.</p> <p>During the measurement, air is pumped from the chamber to an IR gas analyzer (IRGA) and then injected again in the chamber. The CO2 concentration inside the chamber is measured for about 90 seconds and then the rate of concentration change is linearly interpolated (over 60s) to obtain the flux measurements. A detailed description of the sampling method can be found in Magnani et al. (2020).</p> <p>Instrumentation used: accumulation chambers (height: 31.5 cm; area of the base: 363 cm2), LI-COR LI-840 & LI-850 IR spectrophotometers, stainless-steel collars (inserted into the soil to a depth of about 1 cm), portable meteorological stations (pyranometer LSI Lastem DPA053, thermohygrometer LSI Lastem DMA672.1), pt100 soil temperature sensors, SM150T soil moisture sensor.</p>
DCA and GNMDS output for 4640 subplots and 95 vascular plant species in four alpine grasslands
<p>Ordination output from detrended correspondence analysis (DCA) and global non-metric multidimensional scaling (GNMDS).</p> <p>Analyses were performed in R with the <em>vegan</em> package (Oksanen 2022) for the entire data set of 4630 subplots and 95 species' occurrences ('global', indicated by global or missing site name in file names), and for each of four sites: Skjellingahaugen (skj), Gudmedalen (gud), Låvisdalen (lav), and Ulvehaugen (ulv). Access .Rds files with readRDS in R/RStudio.</p> <p>For GNMDS files, k indicates the chosen number of dimensions. See GitHub repository for scripts to produce and perform further analysis with the files in this archive.</p> <p>Analyses performed by EL with scripts based on originals by RH.</p>
Model output for five Hmsc models of alpine grassland communities
<p>Model output from five joint species distribution models made with Hmsc in R. One 'global' model with all data, and one model for each of four sites Skjellingahaugen, Gudmedalen, Låvisdalen, and Ulvehaugen.<br> <br> Omegas are species co-occurrence estimates.</p> <p>Models defined by EL, OO, data formatted by EL, model fit by OO.</p> <p>Scripts for model fitting and presenting output are not published here but follow the generic Hmsc pipeline as published in Ovaskainen & Abrego (2020). Joint Species Distribution Modelling With Applications in R. Cambridge university press. DOI: <a href="https://doi.org/10.1017/9781108591720">https://doi.org/10.1017/9781108591720</a></p> <p> </p>
FIG. 3 in Rodents in grassland habitats: does livestock grazing matter? A comparison of two Alpine sites with different grazing histories
FIG. 3. — Rank/abundance plots for the Carex sempervirens (CS) and Dactylis glomerata (DG) pastoral types. Plots are based on data published by Cavallero et al. (2003, 2007) and refer to: A, the pastoral type of the lightly grazed areas (CS type); B, the abandoned, formerly intensively grazed areas (DG type).
FIG. 2 in Rodents in grassland habitats: does livestock grazing matter? A comparison of two Alpine sites with different grazing histories
FIG. 2. — Box and whisker plots showing the median, first and third quartile and the minimum and maximum values for the log of the captured animals in each plot. Outliers are plotted as open circles.
FIG. 1 in Rodents in grassland habitats: does livestock grazing matter? A comparison of two Alpine sites with different grazing histories
FIG. 1. — Simplified land use in the study area overlaid onto a topographic map. Sampling plots were located within the lightly grazed and in the intensively grazed areas. For the latter areas, in particular, plots were located in sites not used by cattle at present. Plot locations are approximate since we could not leave traps unattended between sessions, with the result that, for each session, plots were not exactly in the same locations as the one before.
Data from: Plant biodiversity responds more strongly to climate warming and anthropogenic activities than microbial biodiversity in the Qinghai-Tibetan alpine grasslands
<p>Biodiversity serves as the fundamental underpinning for ecosystem functions and services. As a result of human-induced global change, there is a growing awareness of the substantial alterations in terrestrial aboveground biodiversity, particularly within alpine regions. However, it remains uncertain whether belowground biodiversity will exhibit similar responses, both in terms of magnitude and manner, to anthropogenic global changes as aboveground biodiversity.</p> <p>Here, we conducted a meta-analysis to assess the impacts of warming, nutrient addition, and grazing on plant and soil microbial biodiversity in alpine grasslands on the Qinghai-Tibetan Plateau, which are known to be climate-sensitive and vulnerable. The analysis included 819 experimental observations from 152 studies, focusing on species richness, Shannon diversity, and Pielou's evenness.</p> <p>We found that plant biodiversity exhibited greater sensitivity to climate warming and anthropogenic activities compared to soil microbial biodiversity. Specifically, plant richness and Shannon diversity were reduced by warming and nutrient addition, while plant evenness was increased by grazing. However, only microbial richness was increased by grazing and microbial evenness was increased by warming slightly.</p> <p>The responses of biodiversity to climate warming and anthropogenic activities were modulated by multiple factors. Specifically, the negative effects of warming on plant biodiversity were more pronounced in long-term experiments under warmer or drier environmental conditions. The negative effects of nitrogen addition on biodiversity were enhanced by the intensity and duration of nitrogen treatment. Appropriate intensity and frequency of grazing were beneficial to sustaining plant biodiversity. Soil microbial biodiversity was weakly regulated, where bacterial Shannon diversity was more sensitive to nutrient addition, while fungal species richness was sensitive to grazing.</p> <p><strong>Synthesis: </strong>Our findings reveal a mismatch between aboveground plant and belowground microbial biodiversity in response to climate warming and anthropogenic activities in alpine grasslands, with plant biodiversity being more sensitive. In the context of future global change, plant biodiversity may be at greater risk than soil microbial biodiversity. In addition, biodiversity responses of different experimental and environmental conditions should be distinguished, and more attention is needed on biodiversity conservation in alpine steppe, or areas with warmer and drier environmental conditions, high-intensity fertilization or heavy grazing. </p>
Vegetation pictures, Alpine grasslands at the Nivolet Plain, Gran Paradiso National Park, Italy 2017-2023
<p>This dataset presents vegetation pictures collected at the Nivolet Plain in Gran Paradiso National Park (GPNP), western Italian Alps, between 2017 and 2023.</p> <p>This collection is linked to the dataset named "Net Ecosystem Exchange, Ecosystem Respiration and meteoclimatic data of Alpine grasslands at Nivolet Plain, Gran Paradiso National Park, Italy 2017-2023" (https://zenodo.org/doi/10.5281/zenodo.7590917) already published in the Zenodo Community "IGG-CNR Critical Zone Observatories".</p> <p>For each measurement, a picture was taken from a nadir perspective, aiming at monitoring the vegetation within the measurement area.</p> <p>The collection is organised as follows.</p> <ul> <li>Main folder: NIVOLET_YEAR (e.g., NIVOLET_2023) <ul> <li>Subfolder: SITE-NAME_YEAR(yyyy format)_MONTH(mm format)_DAY(dd format) (e.g., AL_2023_06_15) <ul> <li>Images: SITE-NAME_YEAR(yyyy format)_MONTH(mm format)_DAY(dd format)_NEE-time(hhmmss format) (e.g., AL_2023_06_15_101400.jpg)</li> </ul> </li> </ul> </li> </ul>
Spatiotemporal dynamics of grassland aboveground biomass in northern China and the alpine region: Impacts of climate change and human activities
<p>We employed CASA model to estimate grassland Net Primary Productivity and aboveground biomass A(AGB) from meteorological and GIMMS Normalized Difference Vegetation Index (NDVI) remote sensing data in northern China. We analyzed the dynamics of grassland AGB and impacts climate change and human activites.</p>
Spatiotemporal dynamics of grassland aboveground biomass in northern China and the alpine region: Impacts of climate change and human activities
<p>We employed CASA model to estimate grassland Net Primary Productivity and aboveground biomass A(AGB) from meteorological and GIMMS Normalized Difference Vegetation Index (NDVI) remote sensing data in northern China. We analyzed the dynamics of grassland AGB and impacts climate change and human activites.</p>
Historical context modifies plant diversity–community productivity relationships in alpine grassland
<p class="MsoNormal"><span>While most studies yield positive relationships between biodiversity (B) and ecosystem functioning (EF), awareness is growing that BEF relationships can vary with ecological context. The awareness has led to increased efforts to understand how contemporary environmental context modifies BEF relationships, but the role of historical context, and the mechanisms by which it may influence biodiversity effects, remains poorly understood.</span></p> <p class="MsoNormal"><span>We examined how historical context alters plant diversity‒community productivity relationships via plant species interactions in alpine grassland. We also tested how historical context modifies interactions between plants and arbuscular mycorrhizal (AM) fungi, which can potentially mediate the above processes.</span></p> <p class="MsoNormal"><span>We studied biodiversity effects on plant community productivity at two grassland sites with different histories related to grazing intensity — heavy versus light livestock grazing — but similar current management. We assembled experimental communities of identical species composition with plants from each of the two sites in disturbed soil from a contemporary heavily grazed grassland, ranging in species richness from one to two, three and six species. Moreover, we carried out a mycorrhizal hyphae-exclusion experiment to test how plant interactions with AM fungi influence plant responses to historical context.</span></p> <p class="MsoNormal"><span>We detected a significantly positive diversity‒productivity relationship that was driven by complementarity effects in communities composed of plants from the site without heavy-grazing history, but no such relationship in plant communities composed of plants from the site with heavy-grazing history</span><span class="MsoCommentReference"><span>.</span></span><span> </span><span>Plants from the site with heavy-grazing history had increased competitive ability and increased yields in low-diversity communities but disrupted complementarity effects in high-diversity communities. </span><span>Moreover, plants of one species from the site with heavy-grazing history benefitted more from AM fungal communities than did plants from the site without such history.</span></p> <p class="MsoNormal"><span>Synthesis: Using the same experimental design and species, communities assembled by plants from two sites with different historical contexts showed different plant diversity</span><span>‒community productivity relationships</span><span>. Our results suggest that historical context can alter plant diversity</span><span>‒community productivity relationships via plant species interactions and potentially </span><span>plant</span><span>‒soil interactions. Therefore, considering historical contexts of ecological communities is of importance for advancing our understanding of long-term impacts of anthropogenic disturbance on ecosystem functioning.</span></p>
FIG. 4 in Rodents in grassland habitats: does livestock grazing matter? A comparison of two Alpine sites with different grazing histories
FIG. 4. — Apodemus Spp. caught during the study.
Pollen limitation and context-dependent alleviating mechanisms in a co-flowering alpine grassland community
<p>1. The consequences of community metrics (e.g., co-flowering diversity and floral density) and plant traits (e.g., pollinator dependency and trait similarity) on pollen limitation may depend on pollinator-mediated competitive or facilitative interactions among plants in co-flowering communities, which could vary with community contexts (i.e. different altitude communities) and under human disturbances (e.g., livestock grazing). However, the mechanisms to alleviate pollen limitation under the different contexts, considering pollinator-mediated interactions among neighbor plants are unclear.</p> <p>2. We investigated pollen limitation under grazing versus ungrazing conditions in low versus high altitude alpine meadows on the Tibetan Plateau to uncover the underlying mechanisms mediating pollen limitation associated with livestock grazing.</p> <p>3. Pollen limitation is prevalent in alpine grasslands, irrespective of community contexts. Grazing exclusion decreased pollen limitation in the two sites but in different ways. In the high-altitude site, pollen limitation was reduced by the exclusion of grazers through increased trait similarity (suggesting facilitation). While pollen limitation was reduced by decreased trait similarity (suggesting competition avoidance) under grazing exclusion in the low-altitude site.</p> <p>4. Synthesis and Applications: This study suggests that flower trait distribution patterns (i.e. trait similarity) influence pollen limitation through reducing competition in the low-altitude site or enhancing facilitation in the high-altitude site under grazing exclusion in alpine grasslands. Our results provide a mechanistic understanding of pollen limitation in co-flowering alpine grassland communities under distinct human disturbances at different altitudes, emphasizing the role of pollinator-mediated interactions among plants on plant reproductive success.</p>
The functioning of alpine grassland ecosystems: climate outweighs plant species richness
<ol> <li><span>The biodiversity–ecosystem functioning relationship has received significant attention in recent decades. It has been widely demonstrated that plant diversity plays a crucial role in enhancing the functioning of terrestrial ecosystems. However, few studies have tested the influence of plant species richness in mediating the impacts of climate on ecosystem functions at large spatial scales. </span></li> <li><span>To address this gap, we utilized data from field surveys across broad climatic gradients at the Qinghai-Tibetan Plateau, China. Our goal was to examine the importance of plant species richness for the functioning of alpine grassland ecosystems, specifically productivity and soil carbon sequestration. </span></li> <li><span>Our results showed strong positive correlations between ecosystem functioning and growing season precipitation as well as species richness. In contrast, there was a negative correlation with growing season temperature. Notably, the positive effect of growing season precipitation on ecosystem functioning outweighed the negative effect of growing season temperature. The indirect effects of growing season precipitation and temperature on ecosystem functioning through changes in species richness were weak. Furthermore, the inclusion of climate factors in the model weakened the relationships between species richness and ecosystem functioning.</span></li> <li><span><em>Synthesis</em>. Our findings demonstrate that climate factors are more important than species richness for the provisioning of ecosystem functions at large spatial scales. In summary, our study underscores the importance of considering climate factors alongside species richness when assessing ecosystem functioning across extensive geographical areas.</span></li> </ol>
Dataset for: Asymmetric response of aboveground and belowground temporal stability to nitrogen and phosphorus addition in a Tibetan alpine grassland
<p><span>Anthropogenic eutrophication is known to impair the stability of aboveground net primary productivity (ANPP), but its effects on the stability of belowground (BNPP) and total (TNPP) net primary productivity remain poorly understood. Based on a nitrogen and phosphorus addition experiment in a Tibetan alpine grassland, we show that nitrogen addition had little impact on the </span><span>temporal stability</span><span> of ANPP, BNPP and TNPP, whereas phosphorus addition reduced the </span><span>temporal stability</span><span> of BNPP and TNPP, </span><span>but not ANPP</span><span>. Significant interactive effects of nitrogen and phosphorus addition were observed on the stability of ANPP because of the opposite phosphorus effects under </span><span>ambient and enriched nitrogen conditions</span><span>. We found that the stability of TNPP was primarily driven by that of BNPP rather than that of ANPP. The responses of BNPP stability cannot be predicted by those of ANPP stability, as the variations in responses of ANPP and BNPP to enriched nutrients, with ANPP increased while BNPP remained unaffected, resulted in asymmetric responses in their stability. The dynamics of grasses, the most abundant plant functional group, instead of community species diversity, largely contributed to the ANPP stability. </span><span>Under the enriched nutrient condition, the synchronization of grasses reduced the grass stability, while the latter had a significant but weak negative impact on the BNPP stability. </span><span>These findings challenge the prevalent view that species diversity regulates the responses of ecosystem stability to nutrient enrichment. Our findings also suggest that the ecological consequences of nutrient enrichment on ecosystem stability cannot be accurately predicted from the responses of aboveground components, and highlight the need for a better understanding of the belowground ecosystem dynamics.</span></p>
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