Contribution of Seagrass Blue Carbon Toward Carbon Neutral Policies in a Touristic and Environmentally-Friendly Island

Introduction

The carbon storage capacity of seagrass has been recognized since the early 1980s (e.g., Smith, 1981) but interest has recently intensified with the recognition of blue carbon ecosystems and their potential to contribute to climate change mitigation (Duarte et al., 2005, 2013; Nellemann and Corcoran, 2009; Mcleod et al., 2011; Fourqurean et al., 2012a). While occupying only 0.1% of the ocean surface, seagrass ecosystems have been estimated to bury 27–44 Tg organic carbon (C_org) year^–1 globally, accounting for 10–18% of the total carbon burial in the oceans, and have soil C_org stocks comparable to those of temperate and tropical forests, mangroves, and tidal marshes (Duarte et al., 2005; Fourqurean et al., 2012a). However, there has been a trend to estimate seagrass C_org storage potential from a limited dataset, based largely on the C_org content of superficial soils and a limited range of seagrass habitats (Fourqurean et al., 2012a; Lavery et al., 2013).

Seagrasses comprise a wide variety of species across a range of depositional environments (Carruthers et al., 2007), and the variability in the sedimentary C_org stocks among seagrass habitats had been found to be high (up to 18-fold; Lavery et al., 2013). The seagrass itself may exert a primary control on C_org storage through its biomass, productivity, and nutrient content (Mateo et al., 1997; Lavery et al., 2013; Miyajima et al., 2015). In addition, both autochthonous (e.g., plant detritus and epiphytes) and allochthonous (e.g., seston and terrestrial matter) sources contribute to the C_org pool in seagrass soils (Hendriks et al., 2008; Kennedy et al., 2010). Moreover, once C_org is buried in the soil, biotic and abiotic factors are likely to control the degree of C_org accumulation and preservation (Mateo et al., 2006). These factors include the rates of sediment accumulation, sediment grain-size, and biochemical composition of the organic matter (Keil and Hedges, 1993; Torbatinejad et al., 2007; Serrano et al., 2016a), and also vary among seagrass meadows (De Falco et al., 2000; Kennedy et al., 2010). As such, considerable variation exists in the estimates of C_org storage in seagrass soils worldwide (ranging from 4.2 to 8.4 Pg C_org; Fourqurean et al., 2012a) and for any given location (Lavery et al., 2013; Campbell et al., 2015; Röhr et al., 2016). In order to improve existing estimates of C_org storage in seagrass ecosystems, further studies that expand the current knowledge on geomorphological and biological factors driving C_org storage are needed (Serrano et al., 2016a; Gullström et al., 2018; Mazarrasa et al., 2018).

The recent focus on carbon trading provides the opportunity to avoid or mitigate CO₂ emissions through the conservation and restoration of seagrass meadows, which rank among the most endangered habitats in terms of global loss rates. Despite recent studies showed that seagrass extent remained stable or increased since 2000s (Carmen et al., 2019), seagrass losses have been estimated at 29% of their global extent since 1880 (Waycott et al., 2009), largely resulting from coastal eutrophication and mechanical disturbance (Short and Wyllie-Echeverria, 1996; Orth et al., 2006). Australia has one of the largest areas of seagrass worldwide (Carruthers et al., 2007) but over the last decades has experienced severe seagrass loss (e.g., Cambridge and McComb, 1984; Arias-Ortiz et al., 2018), even in relatively pristine environments such as in Rottnest Island, Western Australia, a tourism destination but where the deployment of permanent moorings led to fragmented meadows (Walker et al., 1989; Hastings et al., 1995) and CO₂ emissions from seagrass soil C_org stocks (Serrano et al., 2016d).

While there is considerable interest in bringing seagrasses and other blue carbon ecosystems into national accounting and mitigation frameworks, there is also significant interest at a more local scale, with local or regional governments, or even private companies, often exploring the potential to become carbon neutral or offset their carbon emissions (e.g., Gössling, 2009). Therefore, Rottnest Island represents an important target area due to its large seagrass meadows and management strategies to mitigate climate change (RIA, 2018). Rottnest Island Authority (RIA) aims to implement actions to reduce greenhouse gas emissions and to investigate offset plans through revegetation programs (RIA, 2018); hence, the results from this study would be useful to guide potential carbon sequestration strategies in Rottnest Island. As with larger scale assessments, the known variability in seagrass carbon stocks requires that the area and the stocks of the different habitats are accounted for when making assessments.

Here we present the results of an extensive survey of seagrass meadows along Rottnest Island (Perth, Western Australia), which included habitat mapping, to produce regional estimates of soil C_org stocks and sequestration rates, and also to provide insights into the contribution of seagrass conservation to achieve a carbon neutral policy in the Island. While this study focuses on one region, the results obtained contribute to understand the differences in C_org storage between seagrass species, highlighting the importance of accounting for habitat variability when scaling up estimates. Finally, to place our results within a broader context, we compare these data to estimates from global datasets, emphasizing recognized variation across seagrass habitats.

Materials and Methods

Study Site, Sampling, and Laboratory Procedures

Rottnest Island is a marine reserve located 19 km off the coast of Perth (Western Australia, 32°00′07″ S, 115°31′01″ E), surrounded by extensive sub-tidal seagrass ecosystems generally found in sheltered bays and areas protected by reefs (Wells et al., 1993; RIA, 2015; Figure 1). Nine species of seagrass have been recorded at Rottnest Island, the dominant species belonging to the genera Posidonia and Amphibolis (Wells et al., 1993). Posidonia sinuosa, Posidonia australis, Amphibolis antarctica and Amphibolis griffithii all form mono-specific meadows and are considered to be “climax” species (Lavery and Vanderklift, 2002), but can also be found in mixed meadows (Kendrick et al., 2000; Carruthers et al., 2007).

Figure 1. (A) Rottnest Island is located 19 km off the coast of Perth, Western Australia. The symbols depict the coring locations and the species composition of the meadows sampled. (B) Benthic habitat map for Rottnest Island using three HyMap flight lines and limited to regions <15 m water depth. Seagrass habitats represents Posidonia spp. and Amphibolis spp. meadows. Macroalgae habitats represent those dominated by Ecklonia radiata and Sargassum spp.

To assess seagrass soil C_org stocks and accumulation rates, in 2014 we sampled soil cores (N = 24) from extensive seagrass meadows comprising mono-specific meadows of Halophila ovalis (6 cores), mixed meadows of P. australis and P. sinuosa (3 cores), mixed meadows of A. antarctica and A. griffithii (5 cores), and mixed Posidonia spp. and Amphibolis spp. meadows (10 cores) along the north and southeast shores of the island (i.e., Thomson Bay, Stark Bay, Phillip Point, Porpoise Bay, Parakeet Bay, Parker Point, and Geordie Bay; Figure 1 and Supplementary Tables 1). The sites were chosen to be representative of seagrass meadows from a variety of habitats, including differences in biotic (e.g., species composition) and abiotic (e.g., hydrodynamic energy) settings. The cores were sampled within extensive seagrass meadows, and meadow edges were located > 50 m away in all cases.

Undisturbed soil cores were randomly sampled within continuous meadows using PVC pipes (70 mm in diameter, 75 cm long) that were gently hammered into the seafloor at 2–4 m water depth while being rotated to assist with penetration. The corers were sealed before retrieval (i.e., using lids and PVC tape) to avoid losing the unconsolidated sediments contained within the corers. Following retrieval, the core samples were cut into 1 cm thick slices. Each slice was weighed before and after oven drying at 60°C until constant weight [dry weight (DW)] to estimate the dry bulk density (DBD). Then, every second slice was divided into two subsamples by quartering. One subsample was milled and analyzed for C_org and stable carbon isotope composition (δ¹³C), while the other subsample was used for sediment grain-size analyses.

For C_org and δ¹³C analyses, 1 g of ground sample was acidified with HCl 4% until bubbling stopped to remove inorganic carbon, centrifuged (5 min at 3,400 r/min), and the supernatant removed carefully by pipette. Then, the sample was washed with Milli-Q water, centrifuged, and the supernatant removed. The residual samples were re-dried and then encapsulated for C_org analysis using a Micro Cube elemental analyzer (Elementar Analysensysteme GmbH, Hanau, Germany) interfaced to a PDZ Europa 20-20 isotope ratio mass spectrometer (Sercon Ltd., Cheshire, United Kingdom) at the University of California Davis. Carbon isotope ratios are expressed as δ values in parts per thousand (‰) relative to the Vienna PeeDee Belemnite. Replicate assays and standards indicated measurement errors of 0.01% for C_org content and 0.06‰ for δ¹³C. Content of C_org was calculated for bulk (pre-acidified) samples.

For sediment grain-size analysis, a Mastersizer 2000 laser-diffraction particle analyzer was used following digestion of the samples with 10% hydrogen peroxide to remove organic matter. Sediments were classified as coarse sand (<1 and >0.5 mm) medium sand (<0.5 and >0.25 mm), fine sand (<0.25 and > 0.125 mm), and very fine sand plus mud (<0.125 mm), according to a scale adapted from Brown and McLachlan (2010).

Data Analyses

The length of core barrel inserted into the soil and the length of retrieved soil were recorded in order to correct the core lengths for compression effects. The corrected core lengths ranged from 22 to 68 cm, and all variables studied here are referred to the corrected, uncompressed depths. C_org density (g C_org cm^–3) was calculated for each soil depth in each core by multiplying the DBD (g cm^–3) by the C_org concentration (%). For soil depths where C_org content (%) was not analyzed, we extrapolated the %C_org (i.e., by averaging the %C_org between above and below depths) and multiplied the %C_org by the DBD to obtain C_org density (g C_org cm^–3). To allow direct comparisons among sites, the standing stocks per unit area (cumulative stocks; kg C_org m^–2) were standardized to 50 cm thick deposits, which involved extrapolating linearly integrated values of cumulative C_org stocks with depth in 12 out of the 24 cores sampled (i.e., from 30 to 50 cm; r² = 0.98, P < 0.001; Supplementary Figures 1). Accumulation rates of C_org were estimated by dividing the inventories in the 50 cm thick soils by the mean soil accretion rate estimated for seagrass meadows at Rottnest Island (i.e., based on ²¹⁰Pb dating) by Serrano et al. (2016d).

The proportion of autochthonous and allochthonous C_org in the seagrass soil C_org pool was estimated using Stable Isotope Mixing Models in R (“simmr” and “rjags” packages; Parnell et al., 2010). The average δ¹³C values within the top 50 cm of each core were analyzed for the probability of relative organic matter contribution to soil stocks using a one-isotope three-source mixing model (Zencich et al., 2002; Phillips and Gregg, 2003). The δ¹³C signatures of potential autochthonous and allochthonous C_org sources (mean ± SD; −10.8 ± 1.6‰ for seagrass, −17.2 ± 1.1‰ for epiphytes plus macroalgae and microphytobenthos, and −24.2 ± 0.6‰ for seston) were obtained from Waite et al. (2007), Ricart et al. (2015), and Serrano et al. (2016c).

All statistical analyses were performed using univariate general linear mixed model (GLMM) procedures in SPSS v. 14.0. GLMMs were used to accommodate the potential non-independence of samples taken at different depths within the same core, since depth is a proxy for time in the cores, and the unbalanced sampling design. The GLMMs were performed to test for significant effects of species composition (Amphibolis spp., Posidonia spp., H. ovalis, and Posidonia/Amphibolis spp.) on DBD (g cm^–3), C_org concentration (%), C_org content (mg cm^–3), δ¹³C signatures, and sediments < 0.125 mm. Species composition and soil depth (cm) were treated as fixed factors, and study site (Thomson Bay, Stark Bay, Phillip Point, Porpoise Bay, Parakeet Bay, Parker Point, and Geordie Bay) was treated as a random factor (probably distribution: normal; link function: identity). A separate GLMM was run to test the effect of species composition (fixed factor) on cumulative C_org stocks (kg C_org m^–2). All response variables (DBD, C_org concentration, content and stock, δ¹³C signatures, and sediment grain size fractions) were square-root transformed prior to analyses and had homogenous variances. Normality and homoscedasticity of model residuals were determined by visual estimation. Pearson correlation analysis was used to test for significant relationships among the variables studied.

Estimates of Seagrass Area and C_org Storage at Rottnest Island

Three flight lines of HyMap hyperspectral data were flown over Rottnest Island by HyVista Corporation in April 2004 with a ground resolution of 3.5 m. The data were corrected to remove sun-glitter and the influence of the atmosphere and water column, using the Modular Inversion and Processing System (MIPS; Heege and Fischer, 2004; Pinnel, 2007). MIPS uses a physically based process to extract information from the data on the water constituents, bathymetry, bottom cover type, and bottom reflectance, with no external inputs. The hyperspectral data were corrected using three generic bottom cover types: bare sediment, and light and dark submerged aquatic vegetation represented by spectral signatures extracted directly from the image.

The output of MIPS provides the spatial distribution of bare sediment and vegetated regions < 15 m depth within the Rottnest Island Marine Park boundaries. The vegetated regions were further classified to identify seagrass meadows and macroalgae using a hierarchical spectral separation classification algorithm in conjunction with a library of spectral reflectance signatures, measured in situ, describing the dominant benthic habitat components for Rottnest Island (Harvey, 2009). The classification algorithm calculated the probability of each benthic habitat component (e.g., Posidonia spp.) being the dominant component for each image pixel and assigning the pixel to the component with the highest probability. The results of this classification required an additional step using the abiotic variables of mean sea level and wave exposure to systematically correct areas misclassified as seagrass as either intertidal reef (areas above mean sea level) or macroalgae (areas highly exposed to wave action). The seagrass meadows were further classified to those dominated by Posidonia spp. or Amphibolis spp., and macroalgae habitats were classified into those dominated by Ecklonia radiata or Sargassum spp. It should be noted it was not possible to identify Halophila spp. meadows using the data obtained due to its sparse growth and size, which means its spectral reflectance at a pixel level is dominated by the bare substrate. The extent of each habitat type was calculated using the number of pixels multiplied by the area of each pixel. Regional seagrass soil C_org stocks and accumulation rates at Rottnest Island were estimated considering inter-species variability, by multiplying the average C_org stocks and accumulation rates of Posidonia spp., Amphibolis spp., and mixed Posidonia/Amphibolis spp. by their respective extents around the Island.

Results

The total area of seagrass within the Rottnest Island Marine Park was estimated to be 755 ha, with Posidonia spp. occupying 113 ha, Amphibolis spp. 257 ha, and mixed Posidonia/Amphibolis spp. meadows 385 ha. The sediments under seagrass meadows at Rottnest Island were mainly composed of medium and fine sands (70–80% of DW). The DBD ranged from 0.5 to 2.1 g cm^–3, while the C_org content (%) of the soils ranged from 0.05 to 3.8% and the δ¹³C signatures of soil organic matter ranged from −8.6 to −24.5‰. The soil C_org stocks and accumulation rates (in 50 cm thick deposits) across the 24 meadows studied ranged 200-fold from 0.05 to 12.9 kg C_org m^–2 and 0.22 to 58.9 kg C_org m^–2 year^–1 (mean ± SE, 5.1 ± 0.7 kg C_org m^–2 and 23.2 ± 3.2 g C_org m^–2 year^–1, respectively; Table 1).

Table 1. Cumulative organic carbon (C_org) stocks [kg C_org m^–2; mean ± standard error (SE)] and accumulation rates (g C_org m^–2 year^–1) in 50 cm thick soil deposit in seagrass meadows at Rottnest Island, Western Australia.

The DBD, proportion of sediment particles < 0.125 mm, and δ¹³C signatures increased with soil depth within the top 10 cm of Amphibolis spp. and H. ovalis cores, and were relatively constant or declined in the Posidonia spp. and mixed Posidonia/Amphibolis cores (Supplementary Figures 2). Below 10 cm soil depth, DBD, sediment particles < 0.125 mm and δ¹³C signatures remained constant or slightly declined down-core in all meadows, except for the increase in sediment particles < 0.125 mm and δ¹³C signatures after 30 cm depth in H. ovalis cores. The soil C_org content (%) in Posidonia spp. and Amphibolis spp. showed no clear trends with soil depth, but C_org content declined in Posidonia/Amphibolis spp. and H. ovalis cores below 20 cm depth. Overall, there were no significant relationships (P > 0.05) between %C_org and the proportion of sediment particles < 0.125 mm (R² = 0.02), nor between %C_org and δ¹³C signatures (R² = 0.07), except for Halophila cores that showed a weak but statistically significant positive relationship between %C_org and δ¹³C signatures (R² = 0.37; Supplementary Figures 3).

Amphibolis spp. meadows had significantly higher DBD (1.3 ± 0.03 g cm^–3) than Posidonia spp., Posidonia/Amphibolis spp., and H. ovalis meadows (ranging from 1.0 ± 0.03 to 1.1 ± 0.02 g cm^–3; P < 0.001; Figure 2A and Table 2). The C_org content was significantly lower in H. ovalis meadows (0.4 ± 0.1% C_org and 1.4 ± 0.2 mg C_org cm^–3) compared to the other meadows (ranging from 0.9 ± 0.004 to 1.5 ± 0.1% C_org and 11.0 ± 0.5 and 15.6 ± 0.6 mg C_org cm^–3; P < 0.001), while mixed Posidonia/Amphibolis spp. meadows contained higher C_org content (1.5 ± 0.1% C_org and 15.6 ± 0.6 mg C_org cm^–3) than mono-specific Amphibolis spp. meadows (0.9 ± 0.03% C_org and 11.0 ± 0.6 mg C_org cm^–3; P < 0.001; Figures 2B,C). The δ¹³C values of organic matter in Posidonia spp. soils were significantly lower (−16.7 ± 0.6‰) than in Posidonia/Amphibolis spp., Amphibolis spp., and H. ovalis meadows (−13.8 ± 0.2, −13.7 ± 0.3, and −15.0 ± 0.3‰, respectively; P < 0.001; Figure 2E and Table 2). Therefore, the contribution of seagrass-derived organic matter to the soil C_org pool was relatively lower in Posidonia spp. (33 ± 2%) compared to the other meadows (ranging from 53 to 66%; Figure 3 and Supplementary Tables 2). The proportion of sediment particles < 0.125 mm was significantly higher in Amphibolis spp. and Posidonia/Amphibolis spp. (14.6 and 13.5%, respectively) than in Posidonia spp. and H. ovalis meadows (7.3 and 8.7%, respectively; P < 0.001; Figure 2F and Table 2).

Figure 2. Mean ± SE of (A) dry bulk density (g DW cm^–3), (B) C_org content (%), (C) C_org concentration (mg cm^–3), (D) C_org inventories (kg m^–2), (E) δ¹³C values (‰), and (F) fine sediment content (% < 0.125 mm) among seagrass habitats (mono-specific Amphibolis spp., Posidonia spp. and H. ovalis, and mixed Posidonia/Amphibolis spp. meadows).

Table 2. (A) Results of statistical testing (GLMMs) for significant effects of seagrass species and soil depth (cm) on the dry bulk density (g DW cm^–3), organic carbon content (%C_org and g C_org cm^–3), cumulative soil C_org stocks at 50 cm depth (kg m^–2), stable carbon isotope values (δ¹³C), and the content of soil particles < 0.125 mm. (B) Post hoc tests showing differences in the variables studied among seagrass species.

Figure 3. Boxplot displaying the outcomes of the stable isotopic mixing models. Proportion (25, 50, and 75% quantiles) of autochthonous (seagrass) and allochthonous (i.e., epiphytes plus macroalgae plus microphytobenthos, and seston) C_org to the seagrass soil C_org pool (top 50 cm) based on seagrass species (Amphibolis spp., Posidonia spp., Posidonia/Amphibolis spp., and Halophila ovalis).

The C_org stocks and accumulation rates in H. ovalis meadows (1.2 ± 0.6 kg C_org m^–2 and 5.4 ± 0.4 g C_org m^–2 year^–1) were up to fivefold lower than in Posidonia/Amphibolis spp. (6.4 ± 1.0 kg C_org m^–2 and 29.4 ± 1.8 g C_org m^–2 year^–1), Amphibolis (6.4 ± 1.3 kg C_org m^–2 and 29.1 ± 2.6 g C_org m^–2 year^–1), and Posidonia (6.2 ± 1.2 kg C_org m^–2 and 28.5 ± 3.2 g C_org m^–2 year^–1) meadows (P < 0.001), which were similar among them (Figure 2D and Table 1). The total seagrass C_org stocks in 0.5 m thick soils in Rottnest Island, accounting for inter-species variability, were estimated to be 48.1 ± 8.5 Gg C_org. Of this total stock, 34% was contained within monospecific Amphibolis spp. meadows, 14% in monospecific Posidonia spp. meadows, and the remaining 51% in mixed meadows of Posidonia/Amphibolis spp. These contributions are directly proportional to the area of each seagrass habitat. The seagrass meadows in Rottnest Island were estimated to have accumulated 220 ± 17 Mg C_org year^–1 over the last decades. As with C_org stocks, the contribution of each habitat to the total annual sequestration was in direct proportion to their area. The seagrass C_org stocks in Rottnest Island are equivalent to 177 ± 31 Gg CO₂ captured at a rate of 0.81 ± 0.06 Gg CO₂ year^–1 (Table 3).

Table 3. Differences in area (ha), organic carbon (C_org) stocks (in 0.5 m thick soils; kg C_org m^–2) and accumulation rates (g C_org m^–2 year^–1) per unit area, C_org stocks (in 0.5 m thick soils; Gg C_org), and C_org accumulation rates (Mg C_org year^–1) and CO_2–eq (Gg CO₂, Gg CO₂ year^–1) among seagrass habitats at Rottnest Island.

Discussion

Variability in Seagrass C_org Storage Among Habitats

The soil %C_org content in Posidonia spp. (0.9–1.4%), Amphibolis spp. (0.6–0.9%), Halophila spp. (0.05–1.4%), and mixed Posidonia/Amphibolis spp. (0.7–2.3%) meadows measured in this study (Figure 2B) are comparable to global values from meadows dominated by the seagrass P. sinuosa and P. australis (0.1–2.1%), A. antarctica and A. griffithii (0.4–3%), and Halophila spp. (0.6–1.2%; Fourqurean et al., 2012b; Lavery et al., 2013; Serrano et al., 2014; Campbell et al., 2015). The relatively low soil C_org content in Rottnest Island seagrasses (1.15% C_org) compared to the global average (2% C_org; Fourqurean et al., 2012a) resulted mainly from the low C_org content in Halophila spp. meadows and to the fact that global estimates are likely biased by extremely high C_org storage values from some temperate seagrass meadows, especially Posidonia oceanica.

The seagrass soil C_org stocks at Rottnest Island (0.05–12.9 kg C_org m^–2 in 0.5 m thick soils) are in the low range compared to global estimates (ranging from 12 to 83 kg C_org m^–2 in 1 m thick soils; Fourqurean et al., 2012a). However, the global estimates were derived from a limited data set biased by the extremely high C_org content of soils from Mediterranean P. oceanica meadows (Fourqurean et al., 2012a). Recent estimates of soil C_org stocks in seagrass meadows encompassed by low biomass species (e.g., Halodule uninervis, H. ovalis, Halophila stipulacea, Zostera spp., and Thalassia hemprichii) ranged from 0.1 to 5.4 kg C_org m^–2 (in 0.5 m thick deposits; estimated from Campbell et al., 2015; Macreadie et al., 2015; Serrano et al., 2018), which are within the range of C_org stocks estimated for low biomass H. ovalis meadows at Rottnest Island (ranging from 0.05 to 4.2 kg C_org m^–2). In addition, the C_org stocks in meadows with high biomass species (P. australis and P. sinuosa) at Rottnest Island (ranging from 2.7 to 12.9 kg C_org m^–2) is in the higher range of other meadows with similar species composition (e.g., ranging from 0.9 to 3.6 kg C_org m^–2; estimated for 0.5 m thick soils from Rozaimi et al., 2016 and Serrano et al., 2016b), but fourfold higher than previous studies on Amphibolis spp. meadows (1.6 kg C_org m^–2 in 0.5 m thick soils; estimated from Lavery et al., 2013). Hence, despite C_org stocks in Rottnest Island seagrass soils tending to be in the lower range of global estimates, the comparisons above highlight the need to update the global estimate of C_org content in seagrass soils using a more balanced geographical distribution of seagrass meadows, but also accounting for habitat variability (i.e., diversity of morphological traits across species and geomorphology; Mazarrasa et al., 2018).

Seagrass biomass and net primary production have been found to play a key role in C_org storage, with dense meadows formed by large species storing larger amounts of C_org in their soils (Fourqurean et al., 2012a; Lavery et al., 2013; Serrano et al., 2016c). The results obtained in this study support this generalization, with up to fivefold higher C_org stocks in Posidonia spp. and Amphibolis spp. meadows compared to H. ovalis meadows. Seagrass meadows of the genera Posidonia (P. australis and P. sinuosa) and Amphibolis (A. antarctica and A. grifficiae) are composed of large and long-living species with high above- and below-ground biomass (averaging 500 and 1,000 g DW m^–2, respectively), whereas H. ovalis is a small and fast-growing species which forms relatively low biomass meadows (76 g DW m^–2; Duarte and Chiscano, 1999). These differences in biomass likely contributed to the higher C_org stocks in Posidonia/Amphibolis spp. meadows compared to H. ovalis meadows. Another factor that may contribute to higher C_org stocks in monospecific and mixed Posidonia/Amphibolis spp. meadows is their capacity to form bulky roots and rhizomes that can penetrate deep into the soil, helping to more rapidly bury dead roots and rhizomes in deeper, anoxic soils, which favors their preservation (Mateo et al., 2006), further enhanced by the higher recalcitrance of these tissues (Trevathan-Tackett et al., 2017). The higher C_org content (% and mg C_org cm^–3) in mixed Posidonia/Amphibolis spp. meadows compared to monospecific meadows could be related to the higher functional performance (e.g., productivity) of meadows formed by multiple species (Duarte, 2000), as observed in mangroves where monotypic forests have lower C_org stocks than those comprising multiple species (Atwood et al., 2017).

Mud content is a good predictor of soil C_org content in Halophila spp. meadows but not in mixed Posidonia/Amphibolis spp. meadows (Serrano et al., 2016a), where the larger contributions of seagrass matter to soil C_org pools dominates the contributing factors. Consequently, the higher δ¹³C values (typical of seagrasses compared to other source of carbon) in meadows of larger seagrass species have been associated with higher C_org storage (Serrano et al., 2016a). The higher contribution of seagrass-derived C_org to the soil C_org pool in Amphibolis spp. and Posidonia/Amphibolis spp. meadows (ranging from 62 to 66%) support this hypothesis (Figure 3). However, the relatively higher soil C_org stocks in Posidonia spp. meadows were not linked to relatively high seagrass-C_org contributions (33% on average), while the relatively high contribution of seagrass-derived C_org in H. ovalis meadows (averaging 53%) did not entail relatively higher soil C_org stocks. The significant positive relationship between %C_org and δ¹³C values in Halophila spp. meadows is consistent with the previous observation that soil C_org stocks increase with increasing contribution of seagrass-derived C_org in the soil pool (Serrano et al., 2016a). However, the lack of significant relationships between %C_org and particles < 0.125 mm, and between %C_org and δ¹³C within monospecific and mixed Posidonia spp. and Amphibolis spp. meadows precludes any generalizable conclusion about the influence of sediment grain-size and seagrass-detritus contribution on soil C_org storage. Other habitat characteristics known to play a role in seagrass soil C_org storage (e.g., differences in hydrodynamic energy, plant cover, density, and biomass; Mazarrasa et al., 2018) among study sites, which were not considered in this study, may help to explain the observations.

The C_org accumulation rates in Rottnest Island seagrass (23.1 ± 3.2 g C_org m^–2 year^–1 on average) are much lower than global estimates (138 ± 38 g C_org m^–2 year^–1; Duarte et al., 2013). However, the C_org accumulation rates in Posidonia spp. meadows at Rottnest Island (28 ± 3 g C_org m^–2 year^–1) are similar to previous estimates for Posidonia spp. meadows in Australia (12 ± 7 to 26 ± 0.8 g C_org m^–2 year^–1; Marbà et al., 2015; Serrano et al., 2016b), but lower than previous estimates for P. oceanica meadows in the Mediterranean Sea (84 ± 20 g C_org m^–2 year^–1), which are the highest in the world (Serrano et al., 2016b). The low accumulation rates in Halophila meadows (5.4 ± 0.4 g C_org m^–2 year^–1), are similar to previous estimates for low biomass and fast-growing seagrass species (i.e., Zostera spp., T. hemprichii, Enhalus acoroides, and Cymodocea serrulata) from Japan, ranging from 2.1 to 10.1 g C_org m^–2 year^–1 (Miyajima et al., 2015).

Contribution of Seagrasses Toward Carbon Neutrality at Rottnest Island

Seagrasses are widely distributed along the coast at Rottnest Island, occupying 755 ha within the Marine Park (excluding meadows formed by small seagrasses such as Halophila spp.), and store considerable amounts of C_org in their soils. In this study, it was not possible to incorporate inter-species variability in C_org storage (i.e., higher C_org stocks in Posidonia and Amphibolis spp. compared to H. ovalis meadows) because of mapping constrains for Halophila spp. meadows. Thus, there is a need to improve seagrass mapping (i.e., including extent of small and large seagrasses) to robustly estimate seagrass blue carbon ecosystem service at Rottnest Island and globally.

Accounting for C_org storage, we estimated that seagrass meadows at Rottnest Island store ∼48 ± 8 Gg C_org within the top 0.5 m soils, which is equivalent to roughly 48 years of local CO₂ emissions at 2015 rates (3,650 Mg CO₂ year^–1; RIA, 2015). Soil C_org stocks at Rottnest Island have been accumulating at a rate of 0.81 ± 0.06 Gg C_org year^–1 over the last decades, thereby sequestering C_org at a rate equivalent to ∼22% of current annual CO₂ emissions from the Island (ranging from 20 to 24%). This highlights the significant role of seagrass meadows in sequestering CO₂.

The estimates of total C_org storage and CO₂ sequestration in Rottnest Island provided here are overall conservative because: (1) we did not incorporate C_org storage within small meadows such as those formed by H. ovalis due to the lack of knowledge on their extent, (2) we restricted our estimates within the 755 ha of mapped seagrass area within the Rottnest Marine Park (up to 15 m depth), and (3) our estimates only considered the C_org stocks within the top 50 cm of soil, while some habitats may contain deeper seagrass C_org stocks. In addition, the large extent of macroalgae at Rottnest Island (190 ha for canopy-forming macroalgae and 1,192 ha for turf algae; Harvey, 2009) could also contribute to C_org sequestration in marine sediments and the deep ocean (Krause-Jensen and Duarte, 2016). In particular, our results showed that macroalgae (plus epiphytes) contributed 12–45% (28% on average) to the seagrass soil C_org pool, suggesting that the export of macroalgae biomass largely contributes to seagrass blue carbon (Kennedy et al., 2010).

Seagrass ecosystems around Rottnest Island were under threat and declining due to anchoring damage (Hastings et al., 1995), which lead to the loss of seagrass, and their associated carbon sink capacity, while eroding the carbon stocks (Serrano et al., 2016d). The deployment of 893 moorings along the coast of Rottnest Island since 1950s has resulted in the loss of 4.8 ha of seagrass meadows (RIA, 2015), which led to the erosion of existing sedimentary C_org stocks and the lack of further accumulation of C_org (Serrano et al., 2016d). Assuming an average loss of 48 Mg C_org ha^–1 following mooring deployment (Serrano et al., 2016d), we estimate cumulative emissions of 845 Mg CO_2–eq from soil C_org stocks (within 4.8 ha of seagrass loss), and a lack of sequestration of 3.9 Mg CO_2–eq ha^–1 year^–1 (cumulative lack of sequestration over 60 years estimated at 235 Mg CO_2–eq year^–1). Seagrass conservation and restoration measures resulting in enhanced C_org sequestration and/or avoided emissions at Rottnest Island can help offset CO₂ emissions by human activities in the island. For example, the revegetation of the 4.8 ha mooring scar extent could result in enhanced sequestration of 19 Mg CO_2–eq year^–1, which would offset 0.5% of annual CO₂ emissions at Rottnest Island (3,650 Mg CO₂ year^–1; RIA, 2018).

Conclusion

Rottnest Island is a popular tourism destination, with approximately half a million visitors per year, with 150,000 arriving by private vessel (Smallwood and Beckley, 2008). The RIA is committed to increasing the environmental, social, and economic sustainability of the Island through increasing the placement of renewable energy, increasing energy efficiency and actions to promote carbon sequestration through potential revegetation programs. This is reflected in the lower CO₂ emissions at Rottnest Island (0.007 Mg CO₂ per capita¹) compared to the average emissions in Australia (16 Mg CO₂ per capita). Therefore, through the incorporation of seagrass C_org sequestration in national greenhouse gas inventories (IPCC, 2003), Rottnest Island is well positioned to improve its carbon neutral policy. The CO₂ sequestration capacity of seagrass ecosystems provides one means of valuing these ecosystems and would provide economic and development opportunities for coastal communities in Rottnest Island and around the world, thereby potentially generating economic income through carbon trading schemes based on the conservation and restoration of seagrass meadows resulting in enhanced C_org sequestration and/or avoided CO₂ emissions (Kelleway et al., 2017). For instance, the replacement of existing moorings at Rottnest Island for environmental-friendly moorings could contribute to minimize seagrass fragmentation and enhance recolonization of bare areas (Demers et al., 2013), thereby enhancing C_org sequestration and reducing CO₂ emissions.

Despite the low C_org stocks of Halophila meadows it is important not to neglect their contribution to ecosystem dynamics. As they are small pioneer species, in temperate regions they are extremely important in colonizing the gaps and scars created by human and natural disturbances, facilitating the establishment of long-living and large biomass seagrasses such as Posidonia spp. and Amphibolis spp. after disturbance (Duarte et al., 1997; Duarte, 2000). Our results showed that there is a need to incorporate inter-habitat variability in regional estimates of seagrass blue carbon resource, in particular accounting for differences between large and long living seagrass such as Posidonia spp. and Amphibolis spp. vs. small and short living species such as H. ovalis.

Our results contribute to the existing global dataset on seagrass soil C_org storage. Furthermore, the results show a significant potential of seagrass to sequester CO₂, which are particularly relevant in the frame of achieving carbon neutral in environmentally-friendly tourist destinations. Indeed, conservation actions aimed to enhance C_org sequestration and/or avoid CO₂ emissions from disturbed seagrass ecosystems could contribute to offset CO₂ emissions at Rottnest Island, and it will also help to protect one of the most valuable ecosystems in the world considering the ecological services they provide (Costanza et al., 1997).

Data Availability Statement

All datasets generated for this study are included in the article/Supplementary Material.

Ethics Statement

The Ethics Committee of Edith Cowan University has approved this study.

Author Contributions

OS designed the study. CB, OS, MH, and CD carried out the field and laboratory measurements. MH mapped habitat types. CB and OS analyzed the data and drafted the first version of the manuscript. All authors contributed to the writing and editing of the manuscript.

Funding

This work was supported by the ECU Faculty Research Grant Scheme. CB was supported by Brazilian Scholarship Program Science Without Borders. OS was supported by an ARC DECRA (DE170101524) and Edith Cowan University Collaboration Enhancement Scheme.

Conflict of Interest

The authors declare that the research was conducted in the absence of any commercial or financial relationships that could be construed as a potential conflict of interest.

Acknowledgments

The authors are grateful to R. Czarnik, Y. Olsen, I. Hendricks, and C. Salinas for their help in field and laboratory tasks.

Supplementary Material

The Supplementary Material for this article can be found online at: https://www.frontiersin.org/articles/10.3389/fmars.2020.00001/full#supplementary-material

FIGURES 1 | Relationship between extrapolated and measured organic carbon stocks (a) from 30 cm to 50 cm in seagrass soil cores ≥ 50 cm depth.

FIGURES 2 | Changes along soil depth (mean ± SE) in the variables studied based on seagrass species at Rottnest Island.

FIGURES 3 | Biplots showing the relationships among the variables studied in the seagrass cores based on seagrass species.

TABLES 1 | Details of the seagrass cores sampled, including the % compression during coring operations. Core length recovered (cm compressed) and core length corrected for compression (cm decompressed).

TABLES 2 | Mean (±SE) isotopic carbon values (‰) in seagrass soil organic matter. Percentage (%; Mean ± SE) contribution of potential organic sources (i.e., seagrass, epiphytes & macroalgae & microphytoenthos, and seston) into seagrass soils.

TABLES 3 | Dataset used to produce this manuscript.

Footnotes

1. ^ http://data.worldbank.org/indicator/EN.ATM.CO2E.PC

References