Nutrient and dissolved gas fluxes across the sediment-water interface under hypoxic conditions in Waquoit Bay, Massachusetts (USA)
On 7 occasions over the course of 3 years (2011-2013) we conducted hypoxic static core incubations on sediments and water collected in Waquoit Bay Massachusetts (USA) from four stations: Childs River Estuary, Metoxit Point, South Basin, & Sage Lot Pond. The goal of this study was quantify sedime...
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figshare
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Online Access: | https://dx.doi.org/10.6084/m9.figshare.7371110 https://figshare.com/articles/Nutrient_and_dissolved_gas_fluxes_across_the_sediment-water_interface_under_hypoxic_conditions_in_Waquoit_Bay_Massachusetts_USA_/7371110 |
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ftdatacite:10.6084/m9.figshare.7371110 |
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record_format |
openpolar |
institution |
Open Polar |
collection |
DataCite Metadata Store (German National Library of Science and Technology) |
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Environmental Chemistry Oceanography FOS Earth and related environmental sciences Environmental Science 50102 Ecosystem Function |
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Environmental Chemistry Oceanography FOS Earth and related environmental sciences Environmental Science 50102 Ecosystem Function Foster, Sarah Fulweiler, Robinson W. Nutrient and dissolved gas fluxes across the sediment-water interface under hypoxic conditions in Waquoit Bay, Massachusetts (USA) |
topic_facet |
Environmental Chemistry Oceanography FOS Earth and related environmental sciences Environmental Science 50102 Ecosystem Function |
description |
On 7 occasions over the course of 3 years (2011-2013) we conducted hypoxic static core incubations on sediments and water collected in Waquoit Bay Massachusetts (USA) from four stations: Childs River Estuary, Metoxit Point, South Basin, & Sage Lot Pond. The goal of this study was quantify sediment metabolism under water column hypoxia in a shallow, temperate estuarine system. Here we provide a comprehensive dataset of dissolved nutrient (i.e., inorganic nitrogen, phosphorus, and silica) and gas (i.e., di-nitrogen, nitrous oxide, and methane) fluxes across the sediment-water interface measured from static core incubations under hypoxic conditions (defined as oxygen concentrations ≤94 μM, 3 mg/L). Note that these fluxes are published (Foster & Fulweiler 2019). We collected triplicate or quadruplicate sediment cores in PVC tubes (10 cm inner diameter, 30 cm height) from the side of a boat using a pole corer equipped with a one-way valve (Fulweiler et al. 2010; Foster & Fulweiler 2014). We also collected in situ bottom water from each site and filtered onboard (nominally to 0.2μm). We then transported cores and water back to our Boston University laboratory and placed them in a water-bath inside an environmental chamber set to ambient bottom water temperatures. We conducted static core incubations in the dark to determine fluxes across the sediment-water interface (e.g., Banta et al. 1995; Giblin et al. 1997; Fields et al. 2014). Core lids were equipped with magnetic stir bars (Dornblaser et al. 1989) which provided gentle (45 rpm) mixing of the overlying water with minimal suspension of sediments (Hopkinson et al. 2001; Renaud et al. 2008; Heiss et al. 2012). In order to simulate hypoxic conditions we used the natural aerobic respiration of the sediments to consume dissolved oxygen and bring each core to hypoxia. The duration of hypoxic incubations were typically around 1 day (median 22 h, range 7.2-36 h). The median final oxygen concentrations measured in the cores at the end of the hypoxic incubation was 0.85 mg/L. Dissolved inorganic nutrient concentrations were determined with high-resolution digital colorimetry on a SEAL Auto Analyzer 3 with segmented flow injection using standard techniques and chemical analyses (Solorzano 1969; Johnson & Petty 1983; Grasshoff et al. 1999). We directly measured N2 on a quadrupole membrane inlet mass spectrometer (MIMS) using the N2/Ar technique developed by Kana et al. (1994). On four occasions we also collected additional duplicate water samples for the analysis of dissolved greenhouse gases, N2O and CH4. We directly measured dissolved N2O and CH4 using a headspace equilibration technique (Kling et al. 1991; Foster & Fulweiler 2016). We analyzed the vial headspace (after water sample – headspace equilibration) using a gas chromatograph (Shimadzu GC-2014) equipped with a flame ionization detector (FID, for CH4) and an electron capture detector (ECD, for N2O). We measured oxygen concentrations using an optical Luminescent Dissolved Oxygen sensor (Hach LDO 101). Note that on one occasion (6 Aug 2012), absolute N2O flux rates were 1-3 orders of magnitude greater than on the other dates and were significant outliers in the dataset (Foster & Fulweiler 2016). These data are designated with a star (*). In addition, on 2 dates in 2012 there was an issue with the instrument analysis of N2, therefore they are designated as having a measurement issue (m.i.) and were not able to be used in our analyses. Nutrient and greenhouse gas parameters were not measured (n.m.) prior to 2012. In a few instances flux rates we could not determine (c.n.d.) flux rates because there was not a predictable linear relationship between concentration change and time. Please email with questions: sqfoster@bu.edu Sampling Stations CRE = Childs River Estuary (41° 34.805’ N 70°31.826’ W, 1.2 m deep, bottom water salinity 27.3-29.7 psu) MP = Metoxit Point (41° 34.134’ N 70° 31.272’ W, 2.2 m deep, bottom water salinity 29.6-31.3 psu) SB = South Basin (41° 33.404’ N 70° 31.442’ W, 1.8 m deep, bottom water salinity 30.6-31.3 psu)SLP = Sage Lot Pond (41° 33.270’ N 70° 30.584’ W, 1.2 m deep, bottom water salinity 28.9-30.4 psu) Units Incubation Temperature = degrees Celsius O2 uptake = di-oxygen per mole O2 (micromoles per meter squared per hour)NH4+ Flux = ammonium (micromoles per meter squared per hour)DSi Flux = dissolved silica (micromoles per meter squared per hour)PO43- Flux = phosphate (micromoles per meter squared per hour)N2-N Flux = di-nitrogen gas per mol N (micromoles per meter squared per hour)N2O Flux = nitrous oxide (nanomoles per meter squared per hour)CH4 Flux = methane (nanomoles per meter squared per hour) Abbreviations & Symbols Date = dd (day)- month - yy (year)* = outlier value m.i. = measurement issuen.m. = not measuredc.n.d. = could not determine Acknowledgments There are numerous people who contributed to this project. We would like to thank the Waquoit Bay National Estuarine Research Reserve (WBNERR) for their continued multi-year support of our research. All water and sediment samples for this study were collected using WBNERR boats. We are particularly grateful to the following WBNERR employees who assisted with the fieldwork: M.K. Fox, A. Lescher, J. Mora, C. Weidman. We would also like to thank several Fulweiler Lab members and Boston University Marine Program (BUMP) students for their assistance with fieldwork and the laboratory-based core incubation experiments: S. Andrews, A. Banks, S. Buckley, K. Czapla, S. Donovan, D. Forest, E. Heiss, J. Luthringer, M. McCarthy, S. Newell, M.K. Rogener, R. Schweiker, K. Yoshimura. M.K. Rogener and E. Heiss also helped analyze samples for N2/Ar concentrations on the Membrane Inlet Mass Spectrometer (MIMS). K. Czapla and A. Al-Haj conducted analyses for nutrient concentrations using a SEAL auto-analyzer. We also thank Boston University Earth and Environment Department for use of their facilities and their general academic and logistical research support. Text Citations Banta GT, AE Giblin, JE Hobbie, and J Tucker. 1995. Benthic respiration and nitrogen release in Buzzards Bay, Massachusetts. Journal of Marine Research 53: 107–135. Dornblaser MM, J Tucker, GT Banta, KH Foreman, MC O'Brien, and AE Giblin. 1989. Obtaining undisturbed sediment cores for biogeochemical process studies using SCUBA. In, eds. M A Lang and W C Jaap, 97–104. Costa Mesa, CA, USA. Fields L, SW Nixon, C Oviatt, and RW Fulweiler. 2014. Benthic metabolism and nutrient regeneration in hydrographically different regions on the inner continental shelf of Southern New England. Estuarine, Coastal and Shelf Science 148. Academic Press: 14–26. Foster SQ, and RW Fulweiler. 2019. Estuarine sediments exhibit dynamic and variable biogeochemical responses to hypoxia. Journal of Geophysical Research: Biogeosciences, 124. https://doi.org/10.1029/2018JG004663 Foster SQ, and RW Fulweiler. 2016. Sediment nitrous oxide fluxes are dominated by uptake in a temperate estuary. Frontiers in Marine Science 3: Article 40. https://doi.org/10.3389/fmars.2016.00040 Foster SQ, and RW Fulweiler. 2014. Spatial and historic variability of benthic nitrogen cycling in an anthropogenically impacted estuary. Frontiers in Marine Science 1: Article 56. https://doi.org/10.3389/fmars.2014.00056. Fulweiler RW, SW Nixon, and BA Buckley. 2010. Spatial and temporal variability of benthic oxygen demand and nutrient regeneration in an anthropogenically impacted New England estuary. Estuaries and Coasts 33: 1377–1390. https://doi.org/10.1007/s12237-009-9260-y. Giblin AE, CS Hopkinson, and J Tucker. 1997. Benthic metabolism and nutrient cycling in Boston Harbor, Massachusetts. Estuaries 20: 346–364. Grasshoff K, K Kremling, and M Ehrhardt. 1999. Determination of Nutrients. In Methods of Seawater Analysis, eds. K Grasshoff, K Kremling, and M Ehrhardt, 3rd ed., 159–226. Weinheim, Germany: Wiley-VCH, Verlag GmbH, D-69469. Heiss EM, L Fields, and RW Fulweiler. 2012. Directly measured net denitrification rates in offshore New England sediments. Continental Shelf Research 45: 78–86. Hopkinson CS, AE Giblin, and J Tucker. 2001. Benthic metabolism and nutrient regeneration on the continental shelf of Eastern Massachusetts, USA. Marine Ecology Progress Series 224: 1–19. Johnson KS, and RL Petty. 1983. Determination of nitrate and nitrite in seawater by flow injection analysis. Limnology and Oceanography 28: 1260–1266. Kling GW, GW Kipphut, and MC Miller. 1991. Arctic lakes and streams as gas conduits to the atmosphere: Implications for tundra carbon budgets. Science 251: 298-301. Renaud PE, N Morata, ML Carroll, SG Denisenko, and M Reigstad. 2008. Pelagic–benthic coupling in the western Barents Sea: processes and time scales. Deep-Sea Research Part II 55: 2372–2380. Solorzano L. 1969. Determination of ammonia in natural waters by the phenolypochlorite method. Limnology and Oceanography 14: 799–801. |
format |
Dataset |
author |
Foster, Sarah Fulweiler, Robinson W. |
author_facet |
Foster, Sarah Fulweiler, Robinson W. |
author_sort |
Foster, Sarah |
title |
Nutrient and dissolved gas fluxes across the sediment-water interface under hypoxic conditions in Waquoit Bay, Massachusetts (USA) |
title_short |
Nutrient and dissolved gas fluxes across the sediment-water interface under hypoxic conditions in Waquoit Bay, Massachusetts (USA) |
title_full |
Nutrient and dissolved gas fluxes across the sediment-water interface under hypoxic conditions in Waquoit Bay, Massachusetts (USA) |
title_fullStr |
Nutrient and dissolved gas fluxes across the sediment-water interface under hypoxic conditions in Waquoit Bay, Massachusetts (USA) |
title_full_unstemmed |
Nutrient and dissolved gas fluxes across the sediment-water interface under hypoxic conditions in Waquoit Bay, Massachusetts (USA) |
title_sort |
nutrient and dissolved gas fluxes across the sediment-water interface under hypoxic conditions in waquoit bay, massachusetts (usa) |
publisher |
figshare |
publishDate |
2019 |
url |
https://dx.doi.org/10.6084/m9.figshare.7371110 https://figshare.com/articles/Nutrient_and_dissolved_gas_fluxes_across_the_sediment-water_interface_under_hypoxic_conditions_in_Waquoit_Bay_Massachusetts_USA_/7371110 |
long_lat |
ENVELOPE(-67.467,-67.467,-67.583,-67.583) ENVELOPE(66.543,66.543,-70.404,-70.404) ENVELOPE(-65.939,-65.939,-68.664,-68.664) ENVELOPE(-67.950,-67.950,-65.700,-65.700) ENVELOPE(163.933,163.933,-84.967,-84.967) ENVELOPE(-59.533,-59.533,-62.333,-62.333) ENVELOPE(33.999,33.999,67.133,67.133) ENVELOPE(-81.183,-81.183,50.800,50.800) |
geographic |
Arctic Barents Sea Petty McCarthy Fid Renaud Buckley Newell Kana Carroll |
geographic_facet |
Arctic Barents Sea Petty McCarthy Fid Renaud Buckley Newell Kana Carroll |
genre |
Arctic Barents Sea Tundra |
genre_facet |
Arctic Barents Sea Tundra |
op_rights |
Creative Commons Attribution 4.0 International https://creativecommons.org/licenses/by/4.0/legalcode cc-by-4.0 |
op_rightsnorm |
CC-BY |
op_doi |
https://doi.org/10.6084/m9.figshare.7371110 |
_version_ |
1766351292977905664 |
spelling |
ftdatacite:10.6084/m9.figshare.7371110 2023-05-15T15:20:57+02:00 Nutrient and dissolved gas fluxes across the sediment-water interface under hypoxic conditions in Waquoit Bay, Massachusetts (USA) Foster, Sarah Fulweiler, Robinson W. 2019 https://dx.doi.org/10.6084/m9.figshare.7371110 https://figshare.com/articles/Nutrient_and_dissolved_gas_fluxes_across_the_sediment-water_interface_under_hypoxic_conditions_in_Waquoit_Bay_Massachusetts_USA_/7371110 unknown figshare Creative Commons Attribution 4.0 International https://creativecommons.org/licenses/by/4.0/legalcode cc-by-4.0 CC-BY Environmental Chemistry Oceanography FOS Earth and related environmental sciences Environmental Science 50102 Ecosystem Function dataset Dataset 2019 ftdatacite https://doi.org/10.6084/m9.figshare.7371110 2021-11-05T12:55:41Z On 7 occasions over the course of 3 years (2011-2013) we conducted hypoxic static core incubations on sediments and water collected in Waquoit Bay Massachusetts (USA) from four stations: Childs River Estuary, Metoxit Point, South Basin, & Sage Lot Pond. The goal of this study was quantify sediment metabolism under water column hypoxia in a shallow, temperate estuarine system. Here we provide a comprehensive dataset of dissolved nutrient (i.e., inorganic nitrogen, phosphorus, and silica) and gas (i.e., di-nitrogen, nitrous oxide, and methane) fluxes across the sediment-water interface measured from static core incubations under hypoxic conditions (defined as oxygen concentrations ≤94 μM, 3 mg/L). Note that these fluxes are published (Foster & Fulweiler 2019). We collected triplicate or quadruplicate sediment cores in PVC tubes (10 cm inner diameter, 30 cm height) from the side of a boat using a pole corer equipped with a one-way valve (Fulweiler et al. 2010; Foster & Fulweiler 2014). We also collected in situ bottom water from each site and filtered onboard (nominally to 0.2μm). We then transported cores and water back to our Boston University laboratory and placed them in a water-bath inside an environmental chamber set to ambient bottom water temperatures. We conducted static core incubations in the dark to determine fluxes across the sediment-water interface (e.g., Banta et al. 1995; Giblin et al. 1997; Fields et al. 2014). Core lids were equipped with magnetic stir bars (Dornblaser et al. 1989) which provided gentle (45 rpm) mixing of the overlying water with minimal suspension of sediments (Hopkinson et al. 2001; Renaud et al. 2008; Heiss et al. 2012). In order to simulate hypoxic conditions we used the natural aerobic respiration of the sediments to consume dissolved oxygen and bring each core to hypoxia. The duration of hypoxic incubations were typically around 1 day (median 22 h, range 7.2-36 h). The median final oxygen concentrations measured in the cores at the end of the hypoxic incubation was 0.85 mg/L. Dissolved inorganic nutrient concentrations were determined with high-resolution digital colorimetry on a SEAL Auto Analyzer 3 with segmented flow injection using standard techniques and chemical analyses (Solorzano 1969; Johnson & Petty 1983; Grasshoff et al. 1999). We directly measured N2 on a quadrupole membrane inlet mass spectrometer (MIMS) using the N2/Ar technique developed by Kana et al. (1994). On four occasions we also collected additional duplicate water samples for the analysis of dissolved greenhouse gases, N2O and CH4. We directly measured dissolved N2O and CH4 using a headspace equilibration technique (Kling et al. 1991; Foster & Fulweiler 2016). We analyzed the vial headspace (after water sample – headspace equilibration) using a gas chromatograph (Shimadzu GC-2014) equipped with a flame ionization detector (FID, for CH4) and an electron capture detector (ECD, for N2O). We measured oxygen concentrations using an optical Luminescent Dissolved Oxygen sensor (Hach LDO 101). Note that on one occasion (6 Aug 2012), absolute N2O flux rates were 1-3 orders of magnitude greater than on the other dates and were significant outliers in the dataset (Foster & Fulweiler 2016). These data are designated with a star (*). In addition, on 2 dates in 2012 there was an issue with the instrument analysis of N2, therefore they are designated as having a measurement issue (m.i.) and were not able to be used in our analyses. Nutrient and greenhouse gas parameters were not measured (n.m.) prior to 2012. In a few instances flux rates we could not determine (c.n.d.) flux rates because there was not a predictable linear relationship between concentration change and time. Please email with questions: sqfoster@bu.edu Sampling Stations CRE = Childs River Estuary (41° 34.805’ N 70°31.826’ W, 1.2 m deep, bottom water salinity 27.3-29.7 psu) MP = Metoxit Point (41° 34.134’ N 70° 31.272’ W, 2.2 m deep, bottom water salinity 29.6-31.3 psu) SB = South Basin (41° 33.404’ N 70° 31.442’ W, 1.8 m deep, bottom water salinity 30.6-31.3 psu)SLP = Sage Lot Pond (41° 33.270’ N 70° 30.584’ W, 1.2 m deep, bottom water salinity 28.9-30.4 psu) Units Incubation Temperature = degrees Celsius O2 uptake = di-oxygen per mole O2 (micromoles per meter squared per hour)NH4+ Flux = ammonium (micromoles per meter squared per hour)DSi Flux = dissolved silica (micromoles per meter squared per hour)PO43- Flux = phosphate (micromoles per meter squared per hour)N2-N Flux = di-nitrogen gas per mol N (micromoles per meter squared per hour)N2O Flux = nitrous oxide (nanomoles per meter squared per hour)CH4 Flux = methane (nanomoles per meter squared per hour) Abbreviations & Symbols Date = dd (day)- month - yy (year)* = outlier value m.i. = measurement issuen.m. = not measuredc.n.d. = could not determine Acknowledgments There are numerous people who contributed to this project. We would like to thank the Waquoit Bay National Estuarine Research Reserve (WBNERR) for their continued multi-year support of our research. All water and sediment samples for this study were collected using WBNERR boats. We are particularly grateful to the following WBNERR employees who assisted with the fieldwork: M.K. Fox, A. Lescher, J. Mora, C. Weidman. We would also like to thank several Fulweiler Lab members and Boston University Marine Program (BUMP) students for their assistance with fieldwork and the laboratory-based core incubation experiments: S. Andrews, A. Banks, S. Buckley, K. Czapla, S. Donovan, D. Forest, E. Heiss, J. Luthringer, M. McCarthy, S. Newell, M.K. Rogener, R. Schweiker, K. Yoshimura. M.K. Rogener and E. Heiss also helped analyze samples for N2/Ar concentrations on the Membrane Inlet Mass Spectrometer (MIMS). K. Czapla and A. Al-Haj conducted analyses for nutrient concentrations using a SEAL auto-analyzer. We also thank Boston University Earth and Environment Department for use of their facilities and their general academic and logistical research support. Text Citations Banta GT, AE Giblin, JE Hobbie, and J Tucker. 1995. Benthic respiration and nitrogen release in Buzzards Bay, Massachusetts. Journal of Marine Research 53: 107–135. Dornblaser MM, J Tucker, GT Banta, KH Foreman, MC O'Brien, and AE Giblin. 1989. Obtaining undisturbed sediment cores for biogeochemical process studies using SCUBA. In, eds. M A Lang and W C Jaap, 97–104. Costa Mesa, CA, USA. Fields L, SW Nixon, C Oviatt, and RW Fulweiler. 2014. Benthic metabolism and nutrient regeneration in hydrographically different regions on the inner continental shelf of Southern New England. Estuarine, Coastal and Shelf Science 148. Academic Press: 14–26. Foster SQ, and RW Fulweiler. 2019. Estuarine sediments exhibit dynamic and variable biogeochemical responses to hypoxia. Journal of Geophysical Research: Biogeosciences, 124. https://doi.org/10.1029/2018JG004663 Foster SQ, and RW Fulweiler. 2016. Sediment nitrous oxide fluxes are dominated by uptake in a temperate estuary. Frontiers in Marine Science 3: Article 40. https://doi.org/10.3389/fmars.2016.00040 Foster SQ, and RW Fulweiler. 2014. Spatial and historic variability of benthic nitrogen cycling in an anthropogenically impacted estuary. Frontiers in Marine Science 1: Article 56. https://doi.org/10.3389/fmars.2014.00056. Fulweiler RW, SW Nixon, and BA Buckley. 2010. Spatial and temporal variability of benthic oxygen demand and nutrient regeneration in an anthropogenically impacted New England estuary. Estuaries and Coasts 33: 1377–1390. https://doi.org/10.1007/s12237-009-9260-y. Giblin AE, CS Hopkinson, and J Tucker. 1997. Benthic metabolism and nutrient cycling in Boston Harbor, Massachusetts. Estuaries 20: 346–364. Grasshoff K, K Kremling, and M Ehrhardt. 1999. Determination of Nutrients. In Methods of Seawater Analysis, eds. K Grasshoff, K Kremling, and M Ehrhardt, 3rd ed., 159–226. Weinheim, Germany: Wiley-VCH, Verlag GmbH, D-69469. Heiss EM, L Fields, and RW Fulweiler. 2012. Directly measured net denitrification rates in offshore New England sediments. Continental Shelf Research 45: 78–86. Hopkinson CS, AE Giblin, and J Tucker. 2001. Benthic metabolism and nutrient regeneration on the continental shelf of Eastern Massachusetts, USA. Marine Ecology Progress Series 224: 1–19. Johnson KS, and RL Petty. 1983. Determination of nitrate and nitrite in seawater by flow injection analysis. Limnology and Oceanography 28: 1260–1266. Kling GW, GW Kipphut, and MC Miller. 1991. Arctic lakes and streams as gas conduits to the atmosphere: Implications for tundra carbon budgets. Science 251: 298-301. Renaud PE, N Morata, ML Carroll, SG Denisenko, and M Reigstad. 2008. Pelagic–benthic coupling in the western Barents Sea: processes and time scales. Deep-Sea Research Part II 55: 2372–2380. Solorzano L. 1969. Determination of ammonia in natural waters by the phenolypochlorite method. Limnology and Oceanography 14: 799–801. Dataset Arctic Barents Sea Tundra DataCite Metadata Store (German National Library of Science and Technology) Arctic Barents Sea Petty ENVELOPE(-67.467,-67.467,-67.583,-67.583) McCarthy ENVELOPE(66.543,66.543,-70.404,-70.404) Fid ENVELOPE(-65.939,-65.939,-68.664,-68.664) Renaud ENVELOPE(-67.950,-67.950,-65.700,-65.700) Buckley ENVELOPE(163.933,163.933,-84.967,-84.967) Newell ENVELOPE(-59.533,-59.533,-62.333,-62.333) Kana ENVELOPE(33.999,33.999,67.133,67.133) Carroll ENVELOPE(-81.183,-81.183,50.800,50.800) |