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48 results for “belowground biomass”
Spartina alterniflora above- and belowground biomass predictions and inundation intensity as estimated by the Belowground Ecosystem Resiliency Model for U.S. Georgia marshes from 2014 to 2023.
We applied the Belowground Ecosystem Resiliency Model (BERM) to estimate monthly aboveground biomass (AGB) and belowground biomass (BGB) in U.S. Georgia Spartina alterniflora marshes from 2014 to 2023 at 30 m scale. This application involved BERM version 2.0 (https://doi.org/10.5281/zenodo.13306821), which was built using data in the PLT-GCET-2308 dataset (https://dx.doi.org/10.6073/pasta/4a0b715104849d98320fcc34e7cd63a4). Data sources for BERM application included Landsat-8/9, NOAA CO-OPS Station ID: 8670870, Daymet, and USGS 3DEP 2018 DEM. Download and processing steps are described in the BERM code and in metadata methods section. Specific descriptions of data processing are available in model code: https://doi.org/10.5281/zenodo.13306821. Data provided here include model output of AGB estimates, BGB estimates, and calculated inundation intensity. See "Data reporting" method in the metadata for description of data files. For logisitical purposes here we present only select data from the model input and output. All model input data sources as listed in the abstract are publicly available. Model calibration data and code are published as well. Additional predictions not published here include foliar chlorophyll, foliar nitrogen, and leaf area index.
Belowground biomass measurements from the GCE-LTER Seawater Addition Long-Term Experiment (SALTEx) Project
SALTEx (Seawater Addition Long-Term Experiment) is a field experiment designed to simulate saltwater intrusion in a tidal freshwater wetland to predict how chronic (Press) and acute (Pulse) salinization will affect this and other tidal freshwater ecosystems. The SALTEx experiment was initiated in 2012 and consists of 31 field plots, each 2.5 m on a side. There are three treatments (Press, Pulse, and Fresh) and two types of controls (with and without sides), each consisting of six replicates. The Press treatment plots receive regular (4 times each week) additions of a mixture of seawater and fresh river water. Pulse plots receive the same mixture of seawater and river water during September and October, which is historically a time of low flow in the river when natural saltwater intrusion occurs. The Fresh treatment plots receive regular additions of fresh river water. Treatment water is added during low tide to facilitate its infiltration into the soil, and all plots are inundated by astronomical tides at high tide. Belowground biomass was sampled from in each plot in March 2017 after 3 years of dosing.
Above ground plant, belowground stem and root biomass in Arctic Long-term Ecological Research's 2006 moist acidic tussock tundra experimental sites, 2012, Toolik Lake, Alaska.
Above ground plant, belowground stem and root biomass was measured in moist acidic tussock tundra experimental sites established in 2006 by the Arctic Long-term Ecological Research site (ARC-LTER. Control plots and plots amended with three different levels of nitrogen(N) and phosphorus(P), F10 (10 g/m2 N and 5 g/m2 P); F5 (5 g/m2 N and 2.5 g/m2 P); F2 (2 g/m2 N and 1 g/m2 P), were sampled.
Coastal Foredune Belowground Biomass, Aboveground Biomass, and Species Cover
<p>We collected data from cross-shore transects at seven sites; three categorized as unmanaged (i.e., Corolla Reserve, the northern dunes of the US Army Engineer Research and Development Center [ERDC] Field Research Facility [FRF North], and dunes in the southern reaches of that same site [FRF South]) and four categorized as managed (i.e., Southern Shores, Nags Head, Pine Island and Duck). Sediment vibracores (n = 15 managed, 10 unmanaged) were collected between September and December 2020 at the dune toe, dune face, crest and back along a single transect at each site. Cores were stored at 4 °C and processed within one week of collection to prevent root degradation. Cores were bisected longitudinally and the sediment from each half was segmented into 30 cm sections from the ground surface (i.e., 0–30 cm, 31–60 cm, 61–90 cm, 91–120 cm, 121–150 cm). To separate belowground biomass, core sections were wet sieved using stacked 3.36 mm, 1.0 mm and 0.5 mm mesh-size sieves. Living belowground biomass was characterized as the sample portions with roots, rhizomes and belowground stems that were still flexible and did not exhibit signs of decomposition. All other biotic material was classified as non-living biomass (e.g., decayed plant material, twigs, seeds, wrack). Within the living belowground biomass component, live roots were separated from other belowground structures (rhizomes, belowground-stems) and scanned using an Epson Perfection V800 Photo electric scanner calibrated for image analysis with WinRhizo™ Pro 2019a by Regent Instruments (Regent Instruments Inc, Quebec City, Quebec, Canada). Images were analyzed to quantify root surface area by diameter size class. Fine roots were defined as those with < 1 mm diameter. All living and non-living belowground biomass was oven-dried at 60 °C for 72 hours and weighed. </p> <p>Soil organic matter content was quantified by loss-on-ignition following manual removal of roots. Samples (1 g of sediment from each core section) were baked in a muffle furnace at 550 °C for 5 hours and reweighed to estimate soil organic matter content (%). Aliquots (300 mg) of each core segment were submitted to the Cornell Stable Isotope Laboratory for % carbon (C) and % nitrogen (N) analysis. Due to cost, only the top 90 cm of soils were sent for C and N analysis.</p> <p>Vegetation surveys were conducted during Summer 2021. We established vegetation survey plots (0.25 m­­2 plot size) centered on each exact coring location. We estimated vegetation cover by species (within 0.25 m2 plot), cover of bare ground, dead plant cover. Adjacent to the coring plots, aboveground biomass (within a 0.1 x 1 m plot) was collected to complement belowground biomass sampling at all sites except Duck, where grasses had been manually planted and permission to harvest aboveground biomass was not granted to maintain the vegetation on the dune face. Aboveground biomass was oven-dried at 60 °C for 72 hours, weighed and scaled to g m-2.</p> <p><strong>More details can be found in the manuscript: </strong></p> <p>White AE, Cohn N, Davis EH, Hein CJ, Zinnert JC. Coastal dune management affects above and belowground biotic characteristics. Scientific Reports (in press).</p>
OMB01 Microbial biomass in the Belowground Plot Experiment at Konza Prairie (1989-1999)
The purpose of this data set is to monitor long-term changes in microbial biomass on the belowground plots due to the effect on annual burning, mowing and nitrogen and phosphorus fertilization.
PBB01 Belowground Plot Experiment: Aboveground net primary productivity of tallgrass prairie based on accumulated plant biomass
To address the potential interactive effects of fire, aboveground biomass removal, and nutrient amendments on above- and belowground responses, a long-term field experiment was initiated in 1986 as part of the Konza Prairie Long-Term Ecological Research (LTER) program. The general goals of this experiment are: 1) to document both short- and long-term responses of plants and soils to fire, aboveground biomass removal (a surrogate for grazing in these small plots), and nutrient amendments (additions of N and/or P); and 2) to provide a better understanding of the mechanisms underlying tallgrass prairie responses to fire, aboveground biomass removal and nutrient enrichment. Peak foliage biomass is measured annually in late fall (September to October) on the 64 belowground plots. Effects of burning, mowing and N + P additions on aboveground NPP are measured. Two 0.1m2 quadrats harvested per plot). 2003 was the last year the mowing treatment was implemented.
PBB02 Belowground Plot Experiment: Biomass and nutrient content of Rhizomes
To address the potential interactive effects of fire, aboveground biomass removal, and nutrient amendments on above- and belowground responses, a long-term field experiment was initiated in 1986 as part of the Konza Prairie Long-Term Ecological Research (LTER) program. The general goals of this experiment are: 1) to document both short- and long-term responses of plants and soils to fire, aboveground biomass removal (a surrogate for grazing in these small plots), and nutrient amendments (additions of N and/or P); and 2) to provide a better understanding of the mechanisms underlying tallgrass prairie responses to fire, aboveground biomass removal and nutrient enrichment. Standing crops of live and dead rhizomes (0.1 sq. m2 * 20cm deep samples) are taken in late summer periodically from 64 belowground plots. N and P content are determined on live and dead rhizomes. N and P for forb rhizomes are available for some plots in some years.
PBB03 Belowground Plot Experiment: Belowground plot experiment: biomass and nutrient content of Roots
To address the potential interactive effects of fire, aboveground biomass removal, and nutrient amendments on above- and belowground responses, a long-term field experiment was initiated in 1986 as part of the Konza Prairie Long-Term Ecological Research (LTER) program. The general goals of this experiment are: 1) to document both short- and long-term responses of plants and soils to fire, aboveground biomass removal (a surrogate for grazing in these small plots), and nutrient amendments (additions of N and/or P); and 2) to provide a better understanding of the mechanisms underlying tallgrass prairie responses to fire, aboveground biomass removal and nutrient enrichment. Standing crops of live and dead grass roots(0.1 sq. m2 x 20cm deep samples) are taken in late summer periodically from 64 belowground plots. N and P content are determined on live and dead grass roots. N and P concentrations for forb roots are available for some plots in some years.
Above- and belowground biomass of S. alterniflora in elevational marsh planter experiments, Plum Island, MA, PIE LTER
Spartina is grown in experimental elevation planters placed in draining ponds on the salt marsh platform. The planters are constructed from PVC pipes of varying lengths. All of the PVC pipes are open at the bottom, and flush to the mudflat surface of the pond, resulting in the tops of the pipes being situated at various relative elevations within the tidal range. Plants growing in the shorter PVC pipes are flooded for a longer duration of each tidal cycle than plants growing in the taller PVC pipes. The growth response of S. alterniflora when exposed to different flood frequencies is monitored by monthly estimates of biomass (determined non-destructively from plant heights) and by destructive 'harvesting' of all above- and belowground plant material at the end of the growing season.
Above- and belowground biomass of S. patens in elevational marsh planter experiments, Plum Island, MA, PIE LTER.
Spartina patens is grown in experimental elevation planters placed in draining ponds on the salt marsh platform. The planters are constructed from PVC pipes of varying lengths. All of the PVC pipes are open at the bottom, and flush to the mudflat surface of the pond, resulting in the tops of the pipes being situated at various relative elevations within the tidal range. Plants growing in the shorter PVC pipes are flooded for a longer duration of each tidal cycle than plants growing in the taller PVC pipes. The growth response of S. patens when exposed to different flood frequencies is monitored by destructive 'harvesting' of all above- and belowground plant material at the end of the growing season.
Changes in above- versus belowground biomass distribution in permafrost regions in response to climate warming
<p>Permafrost regions contain approximately half of the carbon stored in land ecosystems and have warmed at least twice as much as any other biome. This warming has influenced vegetation activity, leading to changes in plant composition, physiology, and biomass storage in aboveground and belowground components, ultimately impacting ecosystem carbon balance. Yet, little is known about the causes and magnitude of long-term changes in the above- to belowground biomass ratio of plants (η). Here, we analyzed η values based on 3,013 plots and 26,337 plant-specific measurements representing eight sites across the Tibetan Plateau from 1995 to 2021. Our analysis revealed distinct temporal trends in η for three vegetation types: a 17% increase in alpine wetlands, and a decrease of 26% and 48% in alpine meadows and alpine steppes, respectively. These trends were primarily driven by temperature-induced growth preferences rather than shifts in plant species composition. Our findings indicate that in wetter ecosystems climate warming promotes aboveground plant growth, while in drier ecosystems, such as alpine meadows and alpine steppes, plants allocate more biomass belowground. Four process-based biogeochemical models failed to simulate the observed changes in η, which highlights the importance of improved process understanding of the processes driving the response of biomass distribution to climate warming, which is crucial for predicting the future carbon trajectory of permafrost ecosystems.</p>
Decommissioned Site: Mameyes (D04 MAME) Belowground Plant Biomass (Megapit) (repackaging of occurrences published by the NEON Biorepository Data Portal)
These samples are associated with NEON prototype dataset: NEON Decommissioned Site data: Root sampling, chemistry, and isotopes (Megapit) from D04 MAME site (a36e6ce2-d845-13e9-c881-c1d4e5881a53) DOI: 10.48443/j1hp-f273 NEON (National Ecological Observatory Network). NEON Decommissioned Site data: Root sampling, chemistry, and isotopes (Megapit) from D04 MAME site, v1 (10.48443/j1hp-f273). https://doi.org/10.48443/j1hp-f273. Dataset accessed from https://data.neonscience.org on July 7, 2021
Belowground foodweb biomass from moist acidic tundra and dry heath tundra nutrient addition and herbivore exclusion plots (since 1996) sampled Summer 2006
Biomass of belowground community groups (bacteria, fungi, protozoa, nematodes, rotifers, tardigrades) determined for organic soils in moist acidic tundra and dry heath tundra.
Belowground foodweb biomass from moist acidic tundra nutrient addition and greenhouse plots (since 1989) sampled July 2008.
Biomass of belowground community groups (bacteria, fungi, protozoa, nematodes, rotifers, tardigrades) determined for organic and mineral soils in moist acidic tundra sampled in the moist acidic tundra nutient (N&amp;amp;amp;P) addition and greenhouse plots in July 2008.
Belowground foodweb biomass and soil CN and bulk density from moist acidic tundra nutrient addition plots (since 1989, 2006) sampled July 2011.
Biomass of belowground community groups (bacteria, fungi, protozoa, nematodes, rotifers, tardigrades) determined for organic and mineral soils in moist acidic tundra. Soil carbon and nitrogen content, bulk density, and depth are included.
Belowground foodweb biomass from moist acidic tundra nutrient addition plots (since 1989, 1996, 2006) sampled June and August 2010.
Biomass of belowground community groups (bacteria, fungi, protozoa, nematodes, rotifers, tardigrades) determined for organic and mineral soils in moist acidic tundra.
Belowground foodweb biomass and soil CN and bulk density from moist acidic tundra nutrient addition plots (since 2006) sampled August 2012.
Biomass of soil rotifers, tardigrades, enchytraeids, protozoa and nematode groups from organic and mineral soils in moist acidic tundra nutrient addition plots (since 2006) sampled August 2012.
Aboveground plant and belowground stem biomass were measured in moist acidic and moist non-acidic tussock tundra experimental plots, Toolik Field Station, Alaska, Arctic LTER 2000.
Aboveground plant and belowground stem biomass were measured in moist acidic and moist non-acidic tussock tundra experimental plots. Treatments at the acidic site include control and nitrogen (N) plus phosphorus (P) amendments; treatments at the non-acidic site include N, P, N+P, greenhouse warming, and greenhouse+N+P. Note: Version 8 corrected an error where Carex vaginata was listed twice under treatment of "Nitrogen Phosphorus". The tissues with 8 quadrats were "Greenhouse" treatment.
2009 LENS belowground biomass core results
2009 LENS Geotechnical and Biomass Results from 72 hand auger cores (50 cm depth) retrieved from LENS and TIDE project creeks (Sweeney, West, Clubhead, Nelson) in Rowley, MA. Thirty-six of these cores were processed for aboveground and belowground biomass (roots, rhizomes, detritus) . Results for belowground biomass presented here. Above ground biomass results are presented in file STP-LENS-2009-above-biomass. The remainder 36 of these cores were processed for bulk density and bulk organic content (from loss on Iinition, LOI) and results are presented in file STP-LENS-2009-geotechnical.
Fiddler crab impacts from observational study 2020-21: Aboveground & diatom biomass, plant height, percent N, burrow & mussel density, belowground biomass, and organic matter
The fiddler crab, Minuca pugnax, expanded its range into the Gulf of Maine recently and was first observed in the Plum Island Estuary in 2014. In 2020 and 2021, we investigated the impact of this burrowing crab on benthic microalgal biomass, sediment properties and the above- and belowground biomass of the cordgrass, Spartina alterniflora. To accomplish this, we conducted a control-impact study in plots with and without fiddler crabs in three marshes in the PIE-LTER: Sawyer, Clubhead, and Metcalf. In its historical range (i.e., south of Cape Cod), M. pugnax, enhances Spartina aboveground biomass. In contrast, we found that, on average, when fiddler crabs were present, aboveground biomass was 40% lower in the PIE-LTER. We also found that belowground biomass was 30% lower and benthic microalgal biomass was 45% lower when fiddler crabs were present, which is in line with our expectations. Because fiddler crabs reduced the biomass of foundational primary producers in its expanded range, our results imply that M. pugnax can influence other saltmarsh functions such as carbon storage and accretion as they expand north. More broadly, our results suggest that as species expand or shift their range with climate change, not only can they have profound impacts in their new ranges, but that those impacts can be the inverse of what is seen in their historical ranges.
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