The loss of natural carbon sinks, such as seagrass meadows, contributes to grenhouse gas emissions and, thus, global warming. Whereas seagrass meadows are declining in temperate and tropical regions, they are expected to expand into the Arctic with future warming. Using paleoreconstruction of carbon burial and sources of organic carbon to shallow coastal sediments of three Greenland seagrass (Zostera marina) meadows of contrasting density and age, we test the hypothesis that Arctic seagrass meadows are expanding along with the associated sediment carbon sinks. We show that sediments accreted before 1900 were highly 13C depleted, indicative of low inputs of seagrass carbon, whereas from 1940’s to present carbon burial rates increased greatly and sediment carbon stocks were largely enriched with seagrass material. Currently, the increase of seagrass carbon inputs to sediments of lush and dense meadows (Kapisillit and Ameralik) was 2.6 fold larger than that of sparse meadows with low biomass (Kobbefjord). Our results demonstrate an increasing important role of Arctic seagrass meadows in supporting sediment carbon sinks, likely to be enhanced with future Arctic warming.
The loss of natural carbon sinks through land use changes has contributed 32% of the cumulative anthropogenic CO2 emissions since the Industrial Revolution1, supporting a significant fraction of the resulting planetary warming2. Warming, in turn, is leading to further losses of some natural carbon sinks, such as seagrass meadows in the Mediterranean (Posidonia oceanica)3 and in Western Australia4, which rank amongst the most intense carbon sinks in the biosphere5,6.
However, global warming is also leading to a poleward migration of the leading edge of the biogeographical distribution of many terrestrial7 and marine species8. This trend has led to the hypothesis that marine macrophytes, including kelps and seagrass, would likely expand into the Arctic with future warming and reduced ice cover9. Whereas kelps already extend to very high latitudes (e.g. 80°N in Svalbard)10, the northern limit of eelgrass (Zostera marina), the seagrass species growing at highest latitudes in the Arctic11, is set around 70°N in areas influenced by warm Atlantic waters (e.g. in the Arctic coasts of Norway)12 and further south, around 64°N in Iceland13 and Western Greenland14. Hence, seagrass meadows are expected to expand into the Arctic with global warming9,14 and to develop new carbon sinks in the region. However, lack of observational time series preclude verification of these predictions.
Here we use paleoreconstruction of sediment accretion rates and sources of organic carbon to shallow coastal sediments to test the hypotheses that (a) seagrass meadows are expanding in the Arctic, and (b) that their expansion is enhancing carbon sinks in Arctic coastal sediments. We reconstruct the contribution of eelgrass to organic carbon burial in sediments under three contrasting eelgrass meadows in Western Greenland.
Results and Discussion
The stocks of organic carbon (Corg) within the top 10 cm of the sediments ranged from 197 g C m−2 to 595 g C m−2, and the inorganic carbon (Cinorg) stocks were similar (Ameralik) or about 2 times lower (Kapisillit and Kobbefjord) than those of Corg (Table 1). The sediments under the seagrass meadows presented 210Pb concentration profiles that allowed establishing robust age models (Fig. 1), despite mixing may have occurred in the upper 2 cm sediment at Kobbefjord. The presence of a relatively thin mixed layer has limited impact when applying the CRS and the CF:CS (below the mixed layer) models15. Coupling of sediment chronologies with organic carbon concentration revealed recent increases in the Corg concentration of eelgrass sediments, particularly so for the dense seagrass meadow at Kapisillit over the past 40 years (Fig. 2).
The corresponding Corg burial rates since 1900 ranged 10 fold from 1.30 g C m−2 year−1 for that at Ameralik to 10.53 g C m−2 year−1 for the meadow at Kapisillit, with a large increase in the ratio of Corg to Cinorg towards present in all three meadows (Fig. 3), likely reflecting changes in sedimentary supply over time as well as differential diagenesis with sediment depth/age. Burial rates of Corg increased greatly from 1940’s to present in the two meadows (3.5 fold at Kobbefjord; 9.1 fold at Kapisillit) where rates could be resolved over this time period (Fig. 4). For Ameralik, only a few layers could be dated (since 1940) and, hence, we cannot resolve any potential change in carbon burial rates. Hence, the evidence for increased sedimentation rates toward present time is based on limited data and should be, therefore, considered to carry considerable uncertainty.
Analysis of changes in Corg with sediment depth suggested a recent change in sources of Corg to the Greenland sediments examined. In particular, sediments accumulated before 1900 were characterized by highly 13C depleted Corg pools (mean ± SE = −30.44 ± 0.38‰ across all three sites), with Corg pools subsequently becoming progressively 13C-enriched (Fig. 5). The Corg source dominating sedimentary inputs before 1900 could be a combination of phytoplankton (δ13C = −24.7 ± 1.12‰) with land-derived Corg, both from terrestrial vegetation and fossil organic carbon released with glacial melting, which have similar isotopic composition (δ13C extending to −35‰ in both cases)16. However, these sources cannot account for the 13C-enriched Corg pools stored in the sediment since 1900 (Fig. 5), which requires either a novel source more enriched in13C or an increase in the contribution of an existing source enriched in 13C. This is likely to be eelgrass-produced carbon, as the average (±SE) δ13C of present-day eelgrass is −7.24 ± 0.21‰, indicative of highly 13C-enriched organic carbon. The mixing model using the carbon sources before 1900, i.e. business as usual carbon source scenario, and eelgrass carbon as end members indicated an increased contribution of eelgrass to sediment Corg after 1900 in all meadows (Fig. 5). Indeed, the surface sediments in the eelgrass meadow at Kapisillit contain the largest contribution of eelgrass (see small plots in Fig. 5), consistent with the highest eelgrass biomass of these meadows, whereas the sediments at Kobbefjord have the lowest contribution of eelgrass to sediment Corg, consistent with the low eelgrass biomass of Kobbefjord (Table 1)14. Moreover, the contribution of eelgrass material to sediment Corg pool has been increasing since 1900 at Kapisillit and Kobbefjord (see small plots in Fig. 5). It would be unlikely that the depletion of 13C observed in older sediment would result from diagenesis, since decomposition rate of eelgrass is about 8 times slower than that of phytoplankton17. The Corg stocks over the top 10 cm of sediment, where isotope mixing models unambiguously support the contribution of eelgrass, are low when compared to global seagrass Corg stocks within a similar soil thickness (2.0 to 6.0 Mg Corg ha−1 in the meadows studied here compared to 9.6 ± 0.7 Mg Corg ha−1, on average ± SE, recalculated from the global compilation of Fourqurean et al.6).
Warming and reduced ice cover in Greenland fjords have been proposed to be conducive to a poleward expansion of marine macrophytes9,14,18,19, as both light and temperature thresholds become more favourable to support macroalgal and seagrass growth. Indeed, experimental evidence indicates that Greenland current and projected (under IPCC scenarios of greenhouse gas emissions) warming conditions enhance eelgrass growth20. The presence of eelgrass in Greenland fjords was first documented in the Godthåbsfjord system in 183014, and in Kapisillit and Ameralik in 1916 (Herbarium specimens from Greenland Herbarium, Botanical Museum, University of Copenhagen) and 192121. However, eelgrass in Kobbefjord, the population with the smallest extent and biomass among those studied here, wasn’t reported until 200914. Hence, we speculate that while eelgrass meadows have been present in Greenland for at least 180 years, they appear to be expanding and increasing their productivity. This is supported by the rapid growth in the contribution of seagrass-derived carbon to the sediment Corg pool, from less than 7.5% at the beginning of 1900 to 53% at present, observed in the studied meadows. Expansion and enhanced productivity of eelgrass meadows in the subarctic Greenland fjords examined here is also consistent with the on average 6.4-fold acceleration of Corg burial in sediments between 1940 and present.
Seagrass meadows have been shown to rank amongst the most intense carbon-sink ecosystems of the biosphere6,22,23 with conservation and restoration programs aimed at protecting and restoring the carbon stocks and sink capacity lost with global seagrass decline24,25. In contrast, seagrass meadows in Greenland seem to be expanding, propelled by warmer seawater temperature and higher doses of submarine irradiance with reduced ice cover14. The expansion of seagrass in Greenland fjords represents a novel carbon sink, with limited significance at present due to the small size of the meadows. However, the potential for further expansion is huge, as the convoluted Greenland coastline represents about 12% of the global coastline. The poleward latitudinal limit of eelgrass is located at far higher latitudes (70°N) than those studied here (64°N), suggesting that eelgrass, along with other boreal macrophyte species, is likely to expand poleward with decreasing ice cover and higher temperatures9,14,26. Hence, whereas the carbon sink associated with sediments under Greenland eelgrass meadows is likely to be very modest at present, it may reach significant levels along the 21st century.
Whereas the concern globally is in slowing down or stopping altogether further losses of seagrass24,27, we provide evidence here for an increasingly important role of sediments under seagrass meadows in Greenland as a carbon sink, whose significance is likely to increase with further climate warming. Propelling this emerging carbon sink requires protection of extant meadows, as these do not only represent carbon sinks already in operation, but also supply propagules essential for further expansion of this valuable ecosystem.
The study was conducted in 3 subarctic seagrass (Zostera marina) meadows located in 3 fjords of the Godthåbsfjordsystem, near Nuuk (West Greenland), the region that harbours all but one Z. marina meadows reported so far in West Greenland14. The fjords are 17 km to 100 km long, with the inner parts of the branches covered with sea ice from November to May during severe winters and no sea ice in the outer bays14. The tidal amplitude in the region ranges from 2 to 5 m.
Two of the studied seagrass meadows (Ameralik, 64°15′N, 51°35′W; and Kapisillit, 64°28′N, 50°13′W) were located at the inner branches of the Ameralik-Itivleq and Kapisigdlit Kangerdluat fjords whereas the third meadow grew at the middle part of Kobbefjord (64°09′N, 51°33′W). All studied seagrass meadows were permanently submerged, at water depths ranging between 2 and 4 m, and exposed to maximum summer water temperatures of 9 °C at Kobbefjord, to 14–15 °C, at Ameralik and Kapisillit14. The presence of Z. marina meadows at Kapisillit and Ameralik were already documented in 1916 (observer O. Bendixen, herbarium collection, Botanical Museum, Copenhagen, Denmark) and 192121, while the first observations of seagrass at Kobbefjord, a thoroughly investigated area (228 documents including the keyword “Kobbefjord” in citations in Google Scholar, 20 June 2017) date from 2009. The absence of pre-2009 Kobbefjord meadow historical accounts strongly suggests that this meadow is relatively young14. Z. marina at Ameralik and Kapisillit formed lush and extensive meadows, with 100% cover and high above- and belowground biomass (Table 1). Conversely, Z. marina at Kobbefjord developed only few patches of vegetation, with less than 10% cover and lower total summer biomass (Table 1). Olesen et al.14 provide a detailed description of Z. marina dynamics and environmental conditions at the studied sites.
In August 2012, we collected sediment cores (5.2 cm diameter) in seagrass meadows of the 3 study sites. We retrieved 3 cores from Kobbefjord and 4 cores from Ameralik, each being 36–42 cm long, and a single 16 cm long core from the meadow at Kapisillit. The sediment at Kapisilit was extremely rich in clay and it prevented to insert the cores deeper; despite trying we could only collect one sediment core longer than 10 cm. We collected the sediment cores from a boat using a manual sampling device to insert the corer as deep as possible into the sediment. Because of the method to collect the cores, we could not measure sediment compaction due to sampling, but it should be negligible, at least, for Kobbefjord and Ameralik sediments, since they were highly sandy and organic poor. The seagrass meadows sampled extended along the suitable habitat. However, we did not collect samples in bare sediments adjacent to vegetated ones, because their current bare nature may be transient and there is no guarantee that these sediments would not have supported seagrass at some point along the 100 years of sediment carbon burial reconstructed here.
We transported the sediment cores vertically to the Greenland Institute of Natural Resources, Nuuk. In the laboratory, we sliced one core from Ameralik and Kobbefjord every centimeter and the remaining cores every 2 cm. We weighed all sediment samples after oven-drying them at 60 °C for 48 h, and estimated their sediment dry bulk density by dividing sediment dry weight by wet sediment volume. We ground the dried sediment and stored the samples until analysis of organic matter, inorganic carbon concentrations, δ13C and 210Pb concentrations.
Along with the collection of sediment cores we also collected 3 samples of eelgrass leaves, each containing material from different shoots, from each meadow, dried at 60 °C for 48 h and ground them for subsequent analysis of δ13C (see below).
210Pb sediment dating and sediment accretion rates
The cores were dated by means of 210Pb. Concentrations of 210Pb along the upper 10–20 cm of one core at each site were determined by alpha spectrometry through the measurement of the activity of its granddaughter, 210Po, following Sanchez-Cabeza et al.28. Briefly, 200 mg aliquots of each layer were spiked with a known amount of 209Po, acid digested and dissolved into a 100 mL 1 M HCl solution, from which the polonium isotopes were autoplated onto pure silver disks. Polonium emissions were measured by alpha spectrometry using Passivated Implanted Planar Silicon, PIPS detectors (CANBERRA, Mod. PD-450.18 A.M.). Reagent blanks were run in parallel and found to be comparable to the detector backgrounds. Supported 210Pb concentrations were determined by averaging total 210Pb concentrations at the base of each profile. These were comparable to the 226Ra concentrations obtained at selected depths in each core by measuring the emissions of its decay products 214Pb (295 and 352 keV peaks) and 214Bi (609 keV peak) using a high-purity germanium detector (CANBERRA, mod. GCW3523) in calibrated geometries, sealed for 21 days.
The concentration profiles of excess 210Pb used for the age modelling were determined by subtraction of the supported 210Pb from total 210Pb concentrations along each core (Fig. 1), showing a decrease in concentration from the surface to constant concentrations at various depths depending on each core (excess 210Pb horizon). Sediment accumulation rates were calculated by applying the constant flux: constant sedimentation (CF:CS)29 and the constant rate of supply (CRS)30 models, which rendered equivalent results (Table 1).
Organic and inorganic carbon stocks, burial rates and δ13C
We measured the concentration of organic matter (OM, % DW) using the loss of ignition technique along the sediment depth profile at 2 cm resolution, and in subsamples of 3 sediment cores per meadow, except for Kapisillit where only one core was collected. We combusted pre-weighed dry (60 °C) sediment samples at 550 °C for 5 hours and estimated the concentration of organic matter (OM) as:
where W60 is the dry weight of the sample at 60 °C and W550 the weight of the sample after combustion at 550 °C. We estimated the sediment organic carbon concentrations (Corg, %DW) from measured organic matter concentrations (OM, % DW) using the relationship described for seagrasses by Fourqurean et al.6.
We also analyzed the concentration of inorganic carbon (Cinorg, %DW) by conducting a second combustion of the sediment samples at 1000 °C for 2 h to release the CO2 of the carbonate and subsequently calculating the concentration of Cinorg as:
where W1000 was the weight of the sediment sample after the second combustion and 0.27 is the ratio of the atomic weight of carbon (12 g) to the molecular weight of CO2 (44 g) released during carbonate combustion. Along the sediment profiles of each core, we calculated the ratio between organic and inorganic carbon concentrations (Corg: Cinorg) as well as the pools of Corg (g Corg cm−3) and Cinorg (g Cinorg cm−3) by multiplying, respectively, Corg and Cinorg concentrations with the sediment dry bulk density of each sediment sample.
We calculated the stocks of Corg and Cinorg (in g C m−2) within the top 10 cm Z. marina sediments by integrating the Corg and Cinorg pools within the top 10 cm sediment layer and over one meter square of seagrass meadow. Similarly, we calculated the Corg and Cinorg stocks (in g C m−2) accumulated since year 1900 by integrating, respectively, Corg and Cinorg pools in sediments younger than 112 years, using the sedimentation rates obtained from the 210Pb data.
We estimated average annual Corg and Cinorg burial rates (in g C m−2 yr−1) in the Greenland seagrass meadows since year 1900 by dividing, respectively, the Corg and Cinorg stocks accreted since then by 112 years (77 years for Kapisillit since the core was only 16 cm long and, hence, did not encompass an entire century of sedimentation). We also estimated the Corg and Cinorg burial rates over shorter time periods using the sediment age estimates along the sediment profile derived from the CRS 210Pb dating model. We calculated the carbon (Corg or Cinorg) burial rates for a particular time period by dividing the carbon stock accumulated within that period by the length of the time period (in years).
We analyzed the δ13C-signature of the organic carbon in all sediment segments of one core from each seagrass meadow and in the leaves of the seagrass shoots from each Greenland Z. marina meadow. For the sediment samples, the isotopic analyses were conducted after acidifying the samples in order to remove calcium carbonate to avoid bias in the isotopic signature31. Acidification was conducted in a fume hood with saturated HCL for 24 h. The stable carbon isotopic composition was analysed by an isotope ratio mass spectrometer (Thermo fisher scientific). It is reported in the δ notation as the ratio of the 13C to the 12C isotope in the sample (Rsample) relative to that of a standard (Standard) i.e., δ sample = 1000 [(Rsample/Rstandard) − 1]. The primary standard is Vienna Pee Dee Bellemnite (VPDB) and secondary standards are Acetanilide (Schimmelmann) and sucrose.
We tested if the relative contribution (f) of seagrasses to sediment organic carbon increased after year 1900. We did so by applying a two source-mixing model,
that considered Z. marina (δ13Cseagr Ameralik = −7.31 ± 0.02‰, δ13Cseagr Kapisillit = −6.58 ± 0.33‰, δ13Cseagr Kobbefjord = −7.83 ± 0.15‰) and a business as usual carbon source scenario, represented by the average δ13Csed observed in sediments accreted before year 1900 (δ13Csed after 1900 = −30.44 ± 0.38‰), as end members. We corrected for the historical change in the δ13C source signatures due to 13C depletion in the atmospheric CO2 and oceanic DIC δ13C signature towards present derived from the burning of fossil fuels (i.e. Suess effect)32. This was done by applying the model described by Schelske and Hodell33 and modified by Verburg34:
to estimate the δ13C of atmospheric CO2 (δ13Catm) over time (years, Y) since year 1840. These values were subsequently normalized to δ13Catm in year 1840, and the resulting time-dependent depletion in δ13C since1840 was subtracted from the measured δ13Csed for each dated sediment section.
Average (and standard error) values of carbon parameters were calculated from measurements of 3 replicated sediment cores from Ameralik and Kobbefjord while values from a single core were applied from Kapisillit. We used JMP to fit linear trends to sediment profiles of enhanced eelgrass contribution (relative to “business as usual” organic carbon input sources, i.e. those prior 1840) to sediment organic carbon after year 1900.
Ciais, P. et al. Carbon and Other Biogeochemical Cycles. In Climate Change 2013: The Physical Science Basis. Contribution of Working Group I to the Fifth Assessment Report of the Intergovernmental Panel on Climate Change (eds Stocker, T. F. et al.) 465–570 (Cambridge University Press, 2013).
IPCC. Climate Change 2013: The Physical Science Basis. Contribution of Working Group I to the Fifth Assessment Report of the Intergovernmental Panel on Climate Change (eds Stocker, T. F. et al.) (Cambridge University Press, 2013).
Marbà, N. & Duarte, C. M. Mediterranean warming triggers seagrass (Posidonia oceanica) shoot mortality. Global Change Biol. 16, 2366–2375 (2010).
Arias-Ortiz, A. et al. A marine heat wave drives massive losses from the world’s largest seagrass carbon stocks. Nat. Clim Change 8, 338–344 (2018).
Mateo, M. A., Romero, J., Pérez, M., Littler, M. M. & Littler, D. S. Dynamics of millenary organic deposits resulting from the growth of the Mediterranean seagrass Posidonia oceanica. Estuar. Coast. Shelf Sci. 44, 103–111 (1997).
Fourqurean, J. W. et al. Seagrass ecosystems as a significant global carbon stock. Nat. Geosci. 5, 505–509 (2012).
Parmesan, C. & Yohe, G. A globally coherent fingerprint of climate change impacts across natural systems. Nature 421, 37–42 (2003).
Poloczanska, E. S. et al. Global imprint of climate change on marine life. Nat. Clim. Change 3, 919–925 (2013).
Krause-Jensen, D. & Duarte, C. M. Expansion of vegetated coastal ecosystems in the futureArctic. Front. Mar. Sci. 1, 77, https://doi.org/10.3389/fmars.2014.00077 (2014).
Wiencke, C., & Amsler, C.D. Seaweeds and their communities in polar regions. In: Seaweed Biology, Ecological Studies (eds Wiencke, C. & Amsler, C. D.), pp 265–291. Springer-Verlag, Berlin, Heidelberg (2012).
Green, E.P. & Short, F.T. World Atlas of Seagrasses. Prepared by the UIMEP World Conservation Monitoring Centre. University of California Press, Berkeley, USA (2003).
Ostenfeld, C. H. Meeresgräser II — Marine Potamogetonaceae. In Die Pflanzenareale. Sammlung kartographischer Darstellungen von Verbreitungsbezirken der lebenden und fossilen Pflanzen-Familien, -Gattungen und –Arten (eds Diels, L. & Samuelsson, G.) Heft 4, Karte 31–40 (Gustav Fischer Verlag, 1927).
Boström, C. et al. Distribution, structure and function of Nordic seagrass ecosystems: implications for coastal management and conservation. Aquat. Conserv. 24, 410–434 (2014).
Olesen, B., Krause-Jensen, D., Marbà, N. & Christensen, P. B. Eelgrass Zostera marina in subarctic Greenland: dense meadows with slow biomass turnover in cold waters. Mar. Ecol. Prog. Ser. 518, 107–121 (2015).
Oldfield, F. & Appleby, P. Empirical testing of 210 Pb-dating models for lake sediments, Lake sediments Environ. Hist. [online] Available from: https://inis.iaea.org/search/search.aspx?orig_q=RN:15063516 (Accessed 6 September 2016), (1984).
Bhatia, M. P. et al. Organic carbon expoert from the Greenland ice sheet. Geochim. Cosmochim Acta 109, 329–344 (2013).
Enríquez, S., Duarte, C. M. & Sand-Jensen, K. Patterns in decomposition rates among photosynthetic organisms: the importance of detritus C:N:P content. Oecol. 94, 457–471 (1993).
Krause-Jensen, D. et al. Seasonal sea ice cover as principal driver of spatial and temporal variation in depth extension and annual production of kelp in Greenland. Global Change Biol. 18, 2981–2994 (2012).
Marbà, N. et al. Climate change stimulates the growth of the intertidal macroalgae Ascophyllum nodosum near the northern distribution limit. AMBIO 46, S119–S131 (2017).
Beca-Carretero, P., Olesen, B., Marbà, N. & Krause-Jensen, D. Response to experimental warming in northern eelgrass populations: Comparison across a range of temperature adaptations. Mar. Ecol. Prog. Ser., 589, 59–72.
Bendixen, O. Godthaab Distrikt. In Grønland i Tohundredeaaret for Hans Egedes Landing. Meddelelser om Grønland Kommissionen for ledelsen af de geologiske og geografiske undersøgelser i Grønland LXI, Vol. II (eds Amdrup, G. C., Bobé, L., Jensen, A. D. S. & Steensby, H. P.) 176–269 (Bianco Lunos Bogtrykkeri, 1921).
McLeod, E. et al. A blueprint for blue carbon: toward an improved understanding of the role of vegetated coastal habitats in sequestering CO2. Frontiers in Ecology and the Environment 7, 362–370 (2011).
Duarte, C. M., Losada, I. J., Hendriks, I. E., Mazarrasa, I. & Marbà, N. The Role of Coastal Plant Communities for Climate Change Mitigation and Adaptation. Nature Climate Change 3, 961–968 (2013).
Waycott, M. et al. Accelerating loss of seagrasses across the globe threatens coastal ecosystems. Proc. Natl. Acad. Sci., USA 106, 12377–12381 (2009).
Marbà, N. et al. Impact of seagrass loss and subsequent revegetation on carbon sequestration and stocks. J. Ecol. 103, 296–302 (2015).
Jueterbock, A. et al. Climate change impact on seaweed meadow distribution in the North Atlantic rocky intertidal. Ecol. Evol. 3, 1356–1373 (2013).
van Katwijk, M. et al. Global analysis of seagrass restoration: the importance of large-scale planting. J. Appl. Ecol. 53, 567–578 (2016).
Sanchez-Cabeza, J. A., Masqué, P. & Ani-Ragolta, I. 210Pb and 210Po analysis in sediments and soils by microwave acid digestion. Journal of Radioanalytical Nuclear Chemistry 227, 19–22 (1998).
Krishnaswamy, S., Lal, D., Martin, J. M. & Meybeck, M. Geochronology of lake sediments. Earth and Planet. Sci. Lett. 11, 407–414 (1971).
Appleby, P. G. & Oldfield, F. The calculation of lead-210 fates assuming a constant rate of supply of unsupported 210Pb to the sediment. Catena 5, 1–8 (1978).
Kennedy, P., Kennedy, H. & Papadimitriou, S. The effect of acidification on the determination of organic carbon, total nitrogen and their stable isotopic composition in algae and marine sediment. Rapid Commun. Mass Spectrom. 19, 1063–1068 (2005).
Keeling, C. D. The Suess effect: 13carbon-14carbon interrelations. Environ. Int. 2, 229–300 (1979).
Schelske, C. L. & Hodell, D. A. Using carbon isotopes of bulk sedimentary organic matter to reconstruct the history of nutrient loading and eutrophication in Lake Erie. Limnol. Oceanogr. 40, 918–929 (1995).
Verburg, P. The need to correct for the Suess effect in the application of δ13C in sediment of autotrophic Lake Tanganyika, as a productivity proxy in the Anthropocene. J. Paleolimnol. 37, 591–602 (2007).
Núria, M., Dorte, K.-J., Pere, M. & Duarte, C. M. Sediment carbon stores in Greenland seagrass meadows [Dataset]. DIGITAL.CSIC, https://doi.org/10.20350/digitalCSIC/8565 (2018).
This work was funded by EU FP7 (project Opera’s, contract number 308393) and King Abdullah University of Science and Technology (KAUST). DKJ received support from the COCOA project under the BONUS program funded by the EU 7th framework program and the Danish Research Council and from the NOVAGRASS (0603-00003DSF) project funded by the Danish Council for Strategic Research. P.M. was supported by the Generalitat de Catalunya through its grant 2017 SGR-1588. We are grateful to the Greenland Institute of Natural Resources for serving as logistic platform and we direct a special thanks to Flemming Heinrich, for help in the field. Kitte Linding Gerlich and Karina Bomholt Oest, Aarhus University, are thanked for help with laboratory analyses. The study is also a contribution to the Greenland Ecosystem Monitoring program (www.G-E-M.dk), the Arctic Science Partnership (www.asp-net.org) and the ICTA ‘Unit of Excellence’ (MinECo, MDM2015-0552)”.
The authors declare no competing interests.
Publisher's note: Springer Nature remains neutral with regard to jurisdictional claims in published maps and institutional affiliations.
About this article
Cite this article
Marbà, N., Krause-Jensen, D., Masqué, P. et al. Expanding Greenland seagrass meadows contribute new sediment carbon sinks. Sci Rep 8, 14024 (2018). https://doi.org/10.1038/s41598-018-32249-w
Global Change Biology (2020)
Blue Carbon stock in Zostera noltei meadows at Ria de Aveiro coastal lagoon (Portugal) over a decade
Scientific Reports (2019)
Temporal and depth-associated changes in the structure, morphometry and production of near-pristine Zostera marina meadows in western Ireland
Aquatic Botany (2019)
DNA barcoding of the marine macroalgae from Nome, Alaska (Northern Bering Sea) reveals many trans-Arctic species
Polar Biology (2019)