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Fig. 4 in Habitat requirements and occurrence of Crematogaster pilosa (Hymenoptera: Formicidae) ants within intertidal salt marshes

Fig. 4. Logistic regression model (P = 0.03) of the probability of Crematogaster pilosa as a function of brown leaf density between 0.61 and 1.20 m. Stars indicate plots containing ants, and open symbols indicate plots not containing ants. Vertical dashed line represents a 50% probability of ants and occurs at a brown leaf density of 2.5 m−1, which equals 1.5 brown leaves between 0.61 and 1.20 m above the marsh surface.

Fig. 2 in Habitat requirements and occurrence of Crematogaster pilosa (Hymenoptera: Formicidae) ants within intertidal salt marshes

Fig. 2. Mean vegetation heights for marsh plots containing ants (n = 8) and plots not containing ants classified by their dominant vegetation type: short (n = 7) and tall (n = 2). All plots were from Dean Creek and Odum's Marsh. Mean heights are the weighted average of all vegetation counts within plots. Letters above whiskers signify significant difference using Tukey's HSD with P <0.05.

Fig. 1 in Habitat requirements and occurrence of Crematogaster pilosa (Hymenoptera: Formicidae) ants within intertidal salt marshes

Fig. 1. Southern tip of Sapelo Island, Georgia (USA). Location of Crematogaster pilosa observations and vegetation assessments in Odum's Marsh (A) and Dean Creek (C). Presence/absence of ants along Lighthouse Creek (B) from canoe and baited trap survey. Sites containing C. pilosa were labeled "ants", those not containing ants were labeled by their vegetation (i.e., short or tall) based on maximum vegetation height.

Fig. 3 in Habitat requirements and occurrence of Crematogaster pilosa (Hymenoptera: Formicidae) ants within intertidal salt marshes

Fig. 3. Height-specific vegetation density for marsh plots with and without ants in Dean Creek and Odum's Marsh. Vegetation density is the number of vegetation features (i.e., stems and leaves) per vertical meter above an average point on the marsh surface. Integrating vertically produces the average number of vegetation features above a single point. All plots containing Crematogaster pilosa were grouped (ants); plots not containing ants were classified by the maximum vegetation height of Spartina alterniflora (i.e., tall or short). Vegetation density distributions are the means for tall (n = 2), ants (n = 8), and short (n = 7) plots.

opencc-by-4.0Jun 2017View details →

Fig. 1. A in A comparison of two insect collection techniques in oiled and non-oiled salt marshes in Louisiana

Fig. 1. A species accumulation curve for both the sweep net (black) and the vacuum (gray) collection techniques. Dotted lines indicate the 95% confidence interval around each curve. Neither curve reached an asymptote.

Figs 11- 18 in Crane flies (Diptera, Tipuloidea) from southern Neotropical salt marshes: survey with DNA barcoding

Figs 11- 18. Morphological characteres for Tipuloidea genera identification. (11) Gonomyia (Neolipophleps), (12) Gonomyia (Paralipophleps), (13) Molophilus and (14) Ormosia, wings; (15) Rhipidia and (16) Dicranomyia, antennae; (17) Symplecta (Symplecta) and (18) Symplecta (Trimicra), wings. Modified from GELHAUS (2009).

Fig. 2 in Crane flies (Diptera, Tipuloidea) from southern Neotropical salt marshes: survey with DNA barcoding

Fig. 2. DNA barcoding gap analysis, with frequency of intra and interspecific distances in COI sequences among Tipuloidea species.

Figs 3-10 in Crane flies (Diptera, Tipuloidea) from southern Neotropical salt marshes: survey with DNA barcoding

Figs 3-10. Morphological characteres for Tipuloidea genera identification: (3) Tipulidae*, (4) Limoniidae, head; (5) Ozodicera*, antennae. (6) Nephrotoma* and (7) Zelandotipula, wings; (8) Toxorhina*, (9) Geranomyia* and (10) Teucholabis*, head (Sc, Subcostal vein; Rs, Radial sector vein; bm-cu, Basalmedial cubital vein; dm, Discal-medial cell). *Modified from GELHAUS (2009).

Fig. 1 in Crane flies (Diptera, Tipuloidea) from southern Neotropical salt marshes: survey with DNA barcoding

Fig. 1. Sampling areas at salt marshes of the Patos Lagoon Estuary, Rio Grande do Sul, southern Brazil.

opencc-zeroJun 2021View details →

Changes in salt marsh detritivore identity influences on ecosystem multifunctionality

Ecosystems world-wide experience changes in species composition in response to natural and anthropogenic changes in environmental conditions. Research to date has greatly improved our understanding of how species affect focal ecosystem functions. However, because measurements of multiple ecosystem functions have not been consistently justified for any given trophic group, it is unclear whether interpretations of research syntheses adequately reflect the contributions of consumers to ecosystems. Using model communities assembled in experimental microcosms, we examined the relationship between four numerically dominant detritivore species and six ecosystem functions that underpin fundamental aspects of carbon and nitrogen cycling above- and below-ground. We tested whether ecosystem responses to changes in detritivore identity depended upon species trait dissimilarity, food web compartment (aboveground, belowground, mixed), or number of responses considered (one to six). We found little influence of detritivore species identity on brown (i.e. soil-based) processes. Only one of four detritivore species uniquely influenced decomposition, and detritivore species did not vary in their influence on soil nitrogen pools (NO3- and NH4+), or root biomass. However, changes in detritivore identity influenced multiple aboveground ecosystem functions. That is, by serving as prey, ecosystem engineers, and occasionally also as herbivores as well as detritivores, these species altered the strength of aboveground predator-herbivore interactions and plant-shoot biomass. Yet, dissimilarity of detritivore functional traits was not associated with dissimilarity of ecosystem functioning. These results serve as an important reminder that consumers influence ecosystem processes via multiple energy channels and that food web interactions set important context for consumer-mediated effects on multiple ecosystem functions. Given that species are being lost, gained, and redistributed at unprecedented rates, we can anticipate that changes in species identity will have additional ecosystem consequences beyond those predicted by species' primary functional role.

opencc-by-4.0Feb 2023View details →

Rates of greenhouse gas (carbon dioxide, methane and nitrous oxide) fluxes, denitrification-derived N2O and N2 fluxes and nitrification-derived N2O fluxes from salt marsh soils in Quebec, Canada and Louisiana, U.S. under ambient and elevated temperature and nutrient loading.

Dataset used in <a href="https://link.springer.com/article/10.1007/s10533-023-01104-0?utm_source=rct_congratemailt&utm_medium=email&utm_campaign=oa_20231214&utm_content=10.1007/s10533-023-01104-0#citeas">Elevated temperature and nutrients lead to increased N2O emissions from salt marsh soils from cold and warm climates</a>. The dataset contains fluxes calculated from headspace gas samples taken over a 24 hour period from intact soil cores, as well as corresponding environmental data. Intact soil cores (0-15 cm depth, 2.5 cm diameter) were taken at five sampling locations along a 20 m transect using a soil auger or piston corer. Samples were collected along a transect in four marsh sites in Quebec, Canada (La Pocatière: 47°22'24.7"N 70°03'26.3"W) and Louisiana, U.S. (Barataria Basin: 29°33'47.3"N 90°04'22.8"W and 29°29'52.2"N 89°55'00.2"W) from two vegetation types (Sporobolus alterniflorus formerly known as Spartina alterniflora and Sporobolus pumilus formerly known as Spartina patens). In Quebec, the two vegetation zones were in the same marsh whereas in Louisiana two separate marshes, dominated by the relevant vegetation, were chosen. Soil samples were collected on the 20-21st July 2021 from Louisiana and the 9-10th August 2021 from Quebec. Environmental data was collected including in-situ soil temperature and salinity, and gravimetric soil moisture, extractable soil dissolved organic carbon (DOC), extractable soil total dissolved nitrogen (TDN), extractable soil nitrate, extractable soil ammonium, extractable soil soluble reactive phosphate, soil total carbon, soil total nitrogen, soil carbon to nitrogen ratio, soil d13C and soil d15N determined from additional 0-15 cm core samples. This project has received funding from the European Union’s Horizon 2020 Research and Innovation Programme under Grant Agreement no. 838296, a NSERC Discovery Grant and a Natural Environment Research Council grant number (NE/T012323/1). Stable 15N tracers were added to the intact soil cores so that at each location, at each treatment level (ambient and elevated, described below), there was one core receiving no tracer for greenhouse gas fluxes, one core receiving 15N-NO3‑ for denitrification rates and one core receiving 15N-NH4+ for nitrification rates. The cores were incubated at ambient temperature (16 ℃ and 28.1 ℃ for Quebec and Louisiana, respectively) and nutrient concentrations (3.2 NO3-, 2.0 NH4+; 2.9 NO3-, 2.5 NH4+; 0.5 NO3-, 7.3 NH4+ and 5.7 NO3-, 2.8 NH4+ mg g wet soil-1 for Quebec S. alterniflorus, Quebec S. pumilus, Louisiana S. alterniflorus and Louisiana S. pumilus, respectively), and elevated temperature (ambient temperature +5 ℃) and nutrient concentration (double ambient concentration). Gas samples were collected from the headspace of 0-15 cm intact cores in a 20 cm high PVC pipe, capped at the top and bottom to create a 5 cm headspace. Gas samples were analysed for greenhouse gases (GHGs: N2O, CH4, CO2) and 15N in denitrification-derived N2O, denitrification-derived N2 and nitrification-derived N2O. Soil temperature (YSI 30, Baton Rouge, USA or DeltaTrak 11050, Pleasanton, USA) and porewater salinity (YSI 30, Baton Rouge, USA or portable ATC refractometer) were measured in-situ or in the laboratory using the portable refactometer. Additional soil samples were used for multiple analyses; one subsample was extracted with ultrapure water (18.2 MΩ) for DOC and TDN analysis, one subsample was extracted with 2M KCl for NO3- and NH4+, one subsample was extracted with Olsen-P solution (0.5 M NaHCO3, pH 8.5), for soluble reactive phosphate analysis and one subsample was weighed and dried for soil moisture and then finely ground and analysed for total carbon, total nitrogen, d13C and d15N. N2O, CH4 and CO2 concentrations were measured in the gas samples using a gas chromatograph interfaced with a PAL3 autosampler (Agilent 7890A, Agilent Technologies Ltd, USA) fitted with a flame ionisation detector (FID) for CH4 analysis and a micro electron capture detector (mECD) for N2O analysis. CO2 was methanised to CH4 before analysis on the FID. The instrument precision as the relative standard deviation was < 5 % for all of the gases, while the minimum detectable concentration difference (MDCD) was 9 ppb N2O, 72 ppb CH4 and 31 ppm CO2. Potential GHG fluxes were calculated from the linear portion or where the highest production was observed in the concentration-time series ( https://doi.org/10.2134/jeq2003.2436). If fluxes were below the MDCD they were set to zero see (https://doi.org/10.1002/2017JG003783). The 15N content of the N2 and N2O was determined using a continuous flow isotope ratio mass spectrometer (Elementar Isoprime PrecisION; Elementar Analysensysteme GmbH, Hanau, Germany) coupled with a trace-gas pre-concentrator inlet with autosampler (isoFLOW GHG; Elementar Analysensysteme GmbH, Hanau, Germany), with a standard deviation of d15N < 0.05 %. Extractable dissolved organic carbon and total dissolved nitrogen were analysed in soil extractant (ultrapure water 18.2 MΩ, 7:1 of extractant to soil) on a TOC/TDN analyser (TOC VCSn + TMN-1, Shimadzu, Kyoto, Japan), with 50 mg C l-1 and 10 mg l-1 standards resulting in accuracy and precision of 0.3 and ±0.3 mg C l-1, and 0.5 and ±0.3 mg N l-1, respectively. Extractable nitrate+nitrite (assumed to be nitrate) and ammonium were analysed in soil extractant (2M KCl, 5:1 of extractant to soil) using a microplate reader and methods in Sims et al., 1995 (<a href="https://doi.org/10.1080/00103629509369298">https://doi.org/10.1080/00103629509369298</a>) with a limit of detection of 0.1 ppm and accuracy of ±5 %. Extractable phosphate was analysed in soil extractant (Olsen-P solution 0.5M NaHCO3, pH 8.5, 10:1 of extractant to dry soil) using a microplate reader and methods in Jeannotte et al., 2004 (https://doi.org/10.1007/s00374-004-0760-4) with a limit of detection of 1 mg P l-1 and accuracy of ±6 %. Soil total carbon, total nitrogen, d13C and d15N analysis was performed using a continuous flow isotope ratio mass spectrometer (Elementar Isoprime PrecisION; Elementar Analysensysteme GmbH, Hanau, Germany) coupled with an elemental analyser (EA) inlet (vario PYRO cube; Elementar Analysensysteme GmbH, Hanau, Germany). The precision was < 5 % for both C and N and the precision as a standard deviation was < 0.06 % for both d13C and d15N. Results from the experiments were entered into an Excel spreadsheet for ingestion into the Zenodo data repository.

publicOct 2022View details →

Diversity and composition of macroinvertebrate communities in a rare inland salt marsh

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publicSep 2019View details →

Data from: Impacts of nutrient subsidies on salt marsh arthropod food webs: a latitudinal survey

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publicJun 2021View details →

Changes in salt marsh detritivore identity influences on ecosystem multifunctionality

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publicJan 2024View details →

Data from: Promoting success in thin layer sediment placement: effects of sediment grain size and amendments on salt marsh plant growth and greenhouse gas exchange

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openCC0Sep 2021View details →

Turbidity of a Salt Marsh within the Altamaha River estuary, GA, USA, 2015-2017

We measured turbidity along a transect from channel to marsh interior for 1 year, beginning in June 2016 at a salt mash in the Altamaha River estuary. We measured turbidity (NTU) with three optical back scatter sensors to in a shore normal transect, with one in the channel (YSI 6600), and two on the marsh surface. The “marsh edge sensor” was 2.4m from the channel edge (Seapoint, RBR Solo) and the “marsh interior sensor” was 18m from the edge (Seapoint, RBR Duo; Figure 1c). The sensors measured every 15 minutes and were equipped with automatic wipers to reduce biofouling. Following retrieval, the turbidity time series data was filtered to remove any erroneous points and times when the sensors were fouled or exposed (Ganju et al. 2005). Turbidity was then calibrated to suspended sediment concentration with local sediment resulting in the calibration equation SSC (mg/L) =1.33*Sensor Turbidity (NTU) (R2=0.9345, n=26, p<<0.001).

openCC0Sep 2021View details →

Turbidity of a Salt Marsh within the Chesapeake Bay, VA, USA, 2016-2017

We measured turbidity along a transect from channel to marsh interior from December 2015 to January 2017 at a salt mash at the mouth of the York River in the Chesapeake Bay, VA, USA. We measured turbidity (NTU) with three optical back scatter sensors (YSI EXO) to in a shore normal transect, with one in the channel and two on the marsh surface at 1m from the marsh edge and 12m from the marsh edge, respectively. The sensors measured every 15 minutes and were equipped with automatic wipers to reduce biofouling. Following retrieval, the turbidity time series data was filtered to remove any erroneous points and times when the sensors were fouled or exposed (Coleman et al. 2020). Turbidity was then calibrated to suspended sediment concentration with local sediment resulting in the calibration equation SSC (mg/L) =1.667*Sensor Turbidity (NTU)

openCC (other)Aug 2013View details →

Change in marsh surface elevation measured with a Surface Elevation Table (SET) at control plots in a Spartina alterniflora-dominated salt marsh at Law's Point, Rowley River, Plum Island Ecosystem LTER, MA.

A Surface Elevation Table (SET) is used to measure changes in the elevation of the marsh platform at a Spartina alterniflora-dominated marsh on the Rowley River in the Plum Island Ecosystem (PIE) LTER site, MA.

openCC (other)Aug 2013View details →

Change in marsh surface elevation measured with a Surface Elevation Table (SET) at control plots in a Spartina patens-dominated salt marsh at Law's Point, Rowley River, Plum Island Ecosystem LTER, MA.

A Surface Elevation Table (SET) is used to measure changes in the elevation of the marsh platform at a Spartina patens-dominated marsh on the Rowley River in the Plum Island Ecosystem (PIE) LTER site, MA.