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Ocean acidification drives community shifts towards simplified non-calcified habitats in a subtropical−temperate transition zone

Scientific Reportsvolume 8, Article number: 11354 (2018) | Download Citation

Abstract

Rising atmospheric concentrations of carbon dioxide are causing surface seawater pH and carbonate ion concentrations to fall in a process known as ocean acidification. To assess the likely ecological effects of ocean acidification we compared intertidal and subtidal marine communities at increasing levels of pCO2 at recently discovered volcanic seeps off the Pacific coast of Japan (34° N). This study region is of particular interest for ocean acidification research as it has naturally low levels of surface seawater pCO2 (280–320 µatm) and is located at a transition zone between temperate and sub-tropical communities. We provide the first assessment of ocean acidification effects at a biogeographic boundary. Marine communities exposed to mean levels of pCO2 predicted by 2050 experienced periods of low aragonite saturation and high dissolved inorganic carbon. These two factors combined to cause marked community shifts and a major decline in biodiversity, including the loss of key habitat-forming species, with even more extreme community changes expected by 2100. Our results provide empirical evidence that near-future levels of pCO2 shift sub-tropical ecosystems from carbonate to fleshy algal dominated systems, accompanied by biodiversity loss and major simplification of the ecosystem.

Introduction

Rising atmospheric concentrations of carbon dioxide are causing surface seawater pH and carbonate ion concentrations to fall in a process known as ocean acidification1. Marine organisms are expected to differ widely in their responses to this increase in CO2 levels; partially due to the fact that altered carbonate chemistry stresses many organisms (e.g. negative effects on calcification, reproduction, feeding rate and early life-stage survival2), but is a resource for others (e.g. enhanced primary production and carbon fixation rates3). Most studies have focussed on the effects of ocean acidification on isolated organisms, yet these experiments seldom include community and ecosystem-level interactions and so it is difficult to assess how the results apply to natural ecosystems4,5,6.

Volcanic seeps can provide natural analogues for the effects of ocean acidification on the structure of marine ecosystems because they expose entire communities to a lifetime of elevated CO2 levels. Use of CO2 seeps in ocean acidification research has steadily increased over the past decade, with suitable sites now located across temperate7,8,9,10, sub-tropical11, and tropical ecosystems12,13. Most marine organisms have a planktonic stage in their life history, so recruitment into high CO2 seep sites will occur from populations that are not genetically adapted to future ocean acidification conditions. Therefore, the communities in the CO2 seep sites that become established will be comprised of organisms that are able to tolerate higher CO2 and lower carbonate saturation states for their entire lives (including those that live for many years). For clonal organisms, multiple generations of asexually reproducing individuals are exposed over periods of years, such as bryozoans and corals14,15, and seagrasses8,16. A few marine organisms have very limited larval dispersal, and there is evidence that populations of polychaetes at CO2 seeps are genetically distinct17, and that populations of molluscs that hatch benthic larvae have adapted to chronic ocean acidification over multiple generations through dwarfism18.

Since the beginning of the industrial era, atmospheric CO2 has increased from ~280 µatm to present day levels of 400 µatm1, and yet our understanding of the effects of ocean acidification that may have already occurred is limited; with most research focussed on potential impacts over the coming century. A recent study restored the carbonate chemistry saturation state of a coral reef flat to near pre-industrial levels and demonstrated that present-day net community calcification of coral reefs is already impaired by ocean acidification19. Due to the influence of the northward flowing Kuroshio Current20,21 our study region in Japan has naturally low levels of surface seawater pCO2 (280–320 µatm), which are near pre-industrial levels based on the global average (280 µatm; ref.1). This particular chemical setting could therefore provide information on how the increase of CO2 since the pre-industrial period has already affected ecosystems in other parts of the world.

The presence of ecosystem engineers can modify habitats, promote spatial complexity and facilitate the presence of other species22,23. Ocean acidification-driven changes to these habitat-forming organisms may therefore interact with the direct effects on those species residing in the habitat, and lead to lower species diversity in coral reefs, mussel beds and macroalgal habitats5. Previous studies in CO2 seeps have demonstrated consistent patterns of ocean acidification impacts on the structure of marine ecosystems, with the observed ecological shifts in the acidified conditions showing a reorganisation of the community including reduced biodiversity8,24,25, and habitat loss (as well as structural complexity)5,11,12. It is currently unclear, however, how those communities located at the boundaries of biogeographic regions are likely to respond to ocean acidification; in these regions many species overlap at their range margins and may demonstrate reduced fitness and performance relative to their range centre. Here, we investigate the effects of ocean acidification at a biogeographic transition zone on the Pacific coast of Japan. This region is a global biodiversity hotspot26,27 where temperate and subtropical communities overlap, with the co-existence of both canopy-forming fleshy macroalgae and zooxanthellate scleractinian corals. These two groups are key habitat-forming species that provide a complex three-dimensional structure that sustains a diverse ecosystem. Such a location will therefore provide information on the effects of ocean acidification on range limits at subtropical−temperate transition zones globally.

In the present study, we assessed the effects of chronic exposure to ocean acidification on intertidal and subtidal communities around a set of volcanic CO2 seeps off Shikine Island, Japan. We examined the community composition of benthic marine life at sites with reference levels of 300 µatm pCO2 (near pre-industrial levels) and compared them with areas exposed to increasing levels of carbon dioxide gradually up to end-of-the-century pCO2 conditions to provide the first chemical and ecological assessment of the impact of ocean acidification at a subtropical−temperate transition zone.

Methods

Study Site and Carbonate Chemistry

Shikine is a volcanic island east of the Izu peninsula in Japan (34°19′9″ N, 139° 12′18″ E) with many CO2 seeps in shallow waters that we surveyed using RV Tsukuba II. Different stations in the intertidal and subtidal zones (3–6 m below Chart datum) were surveyed and given a classification based on their mean pCO2 levels. Those stations with a similar pCO2 level were then grouped together for subsequent analysis. The groupings used were 300, 400, 1100 and 1800 µatm pCO2 for the intertidal, and 300, 400, 700, 900, and 1500 µatm pCO2 for the subtidal. The intertidal stations included eight ‘300 µatm’ stations, one ‘400 µatm’ station, two ‘1100 µatm’ stations and one ‘1800 µatm’ station. The subtidal included three ‘300 µatm’ stations, one ‘400 µatm’ station, one ‘700 µatm’ station, one ‘900 µatm’ station and one ‘1500 µatm’ station (see Fig. 1 for station locations). The abundance and distribution of rocky shore communities varies greatly in both space and time, even along the same stretch of coast28. Following the suggestion of refs29,30 we used multiple reference stations (eight ‘300 µatm’ pCO2 in the intertidal, and three ‘300 µatm’ pCO2 in the subtidal) to assess the variability of ‘normal’ rocky shore communities to compare with our high CO2 stations.

Figure 1
Figure 1

Study area (Shikine-Jima, Japan) showing intertidal and subtidal stations, and the spatial variability in pCO2. The spatial distribution of pCO2 was computed using the nearest neighbour algorithm in ArcGIS 10.2 software (http://www.esri.com/software/arcgis/). ‘*’Indicates sites where 24-hour measurements of carbonate chemistry were taken.

To describe the carbonate chemistry of the survey stations, pH, temperature, salinity and total alkalinity (TA) were measured through in situ measurements and/or discrete sampling at the respective stations using both a YSI sensor (YSI Pro Plus, USA) and a TOA-DKK multisensor (WQ-22C, TOA-DKK, Japan) in June 2015. Intertidal stations were surveyed by fixing the sensors to the shore (50 cm below the low water mark), with discrete samples collecting surface water. Subtidal stations were surveyed by fixing the sensors to the seafloor at 5–6 m depth. Discrete samples in the subtidal surveys were taken by SCUBA divers close to the bottom (5–6 m depth). Long term monitoring of pH, temperature, conductivity and dissolved oxygen of the bottom water at the ‘300 µatm’ and ‘900 µatm’ pCO2 stations was carried out in June 2016 using durafet pH sensors (Seafet, Sea-Bird Scientific, Canada) calibrated on the total scale, Hobo conductivity loggers (U24-002-C) and Hobo dissolved oxygen data loggers (U26-001) (Bourne, Onset, USA) with the sensors fixed 30 cm above the seafloor at a depth of 5–6 m. A Horiba multi-parameter meter (U-5000G, Horiba Ltd, Kyoto Japan) coupled with a GPS (eTrex30x, Garmin) was used to document the spatial variation in carbonate chemistry, where we mapped the spatial distribution of pCO2 using the nearest neighbour interpolation algorithm in ArcGIS (ESRI, New York, USA), see Fig. 1.

All pH meters, with the exception of the factory calibrated SeaFET sensors, were regularly calibrated to the NBS pH scale using three buffers 4.01, 7.00 and 10.01 (Thermo Scientific, USA). Total alkalinity of the intertidal stations was measured at the ‘300 µatm’ (n = 6), ‘400 µatm’ (n = 4), ‘1100 µatm’ (n = 4) and ‘1800 µatm’ (n = 3) stations. For the subtidal zone, bottom water samples were collected for TA measurements at the ‘300 µatm’ (n = 10), ‘400 µatm’ (n = 3), ‘700 µatm’ (n = 11), ‘900 µatm’ (n = 14), and ‘1500 µatm’ (n = 14) stations. Water samples were immediately filtered at 0.45 μm using disposable cellulose acetate filters (Dismic, Advantech, Japan) and stored at room temperature in the dark until measurement. TA was measured by titration (785 DMP Titrino, Metrohm) with HCl at 0.1 mol l−1, and then calculated from the Gran function between pH 4.2 and 3.0. The titrations were cross-validated using a working standard (SD: ± 9 μmol kg−1) and against certified reference material purchased from the A.G. Dickson laboratory. Carbonate chemistry parameters were calculated using the CO2SYS software31. Measured pHNBS, TA, temperature and salinity were used as the input variables, alongside the disassociation constants from Mehrbach et al.32, as adjusted by Dickson et al.33, KSO4 using Dickson34, and total borate concentrations from Uppström35.

Biological Survey

Percent cover of intertidal macroflora and encrusting fauna were visually assessed using 25 × 25 cm quadrats. Other sessile macroinvertebrates were counted in 50 × 50 cm quadrats. In both cases, 10–15 replicate quadrats were haphazardly deployed at least a metre apart on steeply sloping rock faces at each station. Macroalgae were grouped as: ‘crustose coralline algae’, ‘non-calcareous encrusting algae’ (such as Peyssonneliaceae spp.) and ‘fleshy algae’ (typically < 5 cm in height such as corticated Ishige okamurae, filamentous Chaetomorpha spiralis, and foliose Ulva spp.). Some fauna were surveyed as % cover, viz. ‘sponges’, ‘hard corals’, ‘barnacles (>1 cm)’, ‘barnacles (<1 cm)’, ‘anemones’ and ‘colonial ascidians’. Groups of invertebrates that were counted as numbers of individuals were ‘serpulids’, ‘spirobids’, ‘mussels’, ‘oysters’, ‘chitons’, ‘carnivorous gastropods’, ‘herbivorous gastropods’ and ‘decapods’. The community structure of shallow subtidal rock was assessed by SCUBA diving using haphazardly placed 50 × 50 cm digital photoquadrats (n = 8–11) at the seven stations of ‘300 µatm’, ‘400 µatm’, ‘700 µatm’, ‘900 µatm’, and ‘1500 µatm’ pCO2 levels. Photographs were analysed using ImageJ36 by overlaying 64 points on a grid, and recording the features and organisms at each point. Coverage in the photoquadrats was grouped as follows: ‘canopy-forming algae’ (5–50 cm in height), ‘low-profile algae’ (<5 cm in height), ‘turf algae’ (filamentous algae and microalgae), ‘non-calcareous encrusting algae’, ‘branched coralline algae’, ‘crustose coralline algae’, ‘hard corals’, ‘soft corals’ and ‘rock’.

In order to assess differences in species richness between the CO2 levels (since taxonomic groups were used to evaluate community changes across stations), species diversity was assessed during 30-minute searches in the intertidal zone at a ‘300 µatm’ station and a ‘1100 µatm’ station. Species richness in the subtidal zone at ‘300 µatm’, ‘400 µatm’ and ‘900 µatm’ stations was assessed by identifying the different species observed in the photoquadrats. The taxonomic groups that were assigned to the species observed in the intertidal and subtidal zones are shown in Tables S1 and S2.

For the statistical analyses, the stations were grouped based on their mean pCO2 classification (see ‘Methods: Study Site and Carbonate Chemistry’). These groups were: ‘300 µatm’, ‘400 µatm’, ‘1100 µatm’ and ‘1800 µatm’ in the intertidal zone, and ‘300 µatm’, ‘400 µatm’, ‘700 µatm’, ‘900 µatm’ and ‘1500 µatm’ in the subtidal zone. Taxonomic groups were individually compared across CO2 levels using the Kruskal-Wallis test, with Fisher’s least significant difference (Bonferroni-adjusted) as a post-hoc test (statistical significance tested at p < 0.05; with results for individual taxonomic groups presented in full in Table S3). All statistical analyses were performed using R software (Version 3.2.4) with the Kruskal function (agricolae package).

The variation in habitat complexity along pCO2 gradients was assessed based on the abundance of sessile taxa, along with a rank (between 0 and 5) for that taxon representing the biogenic habitat complexity provided. These ranks were: Minimum habitat complexity = 0, e.g. all encrusting algae; Very low complexity = 1, e.g. small spirorbids and small barnacles; Low complexity = 2, e.g., turf and low-profile fleshy algae, sponges and non calcifying anthozoans; Moderate complexity = 3, e.g. branched coralline algae and sparse oysters; High complexity = 4, e.g. canopy-forming algae, clumps of mussels; Exceptionally high habitat complexity = 5, e.g. hard corals (see Supporting Information, Table S3). The habitat complexity was calculated as follows: the abundance of each taxonomic group was normalised (using the decostand function, vegan package) and then had the rank (0–5 score) applied, providing a habitat complexity score for each quadrat. In order to provide a relative measure across the pCO2 sites, the habitat complexity score was normalised to between 0 and 1, where the quadrat showing the maximum complexity had a score of 1. These scores were then used to calculate the mean habitat complexity and its variability (standard error) for the different pCO2 stations.

Results

Seawater carbonate chemistry

There were two areas with permanently high pCO2 located in the northern part of the bay where CO2 was bubbling up through the seabed (Fig. 2). Our stations closest to these seeps had mean pCO2 1773 ± 1487 µatm (‘1800 µatm’, intertidal) and 1552 ± 540 µatm (‘1500 µatm’, subtidal) (Figs 1, S1 and S2; Table 1). Variations in pCO2 over time were greatest at the highest pCO2 stations, the 10th and 90th percentiles are shown in Table 1 and boxplots showing the variation ranges of each parameters are shown in Fig. 2 and Supplementary Figs S1 and S2. These high levels of pCO2 corresponded to mean ΩA values of 1.33 ± 0.67 at station ‘1800 µatm’ and 0.94 ± 0.33 at station ‘1500 µatm’, with minimum levels of ΩA observed being 0.30 and 0.60, respectively. Farther from the seep sites, intertidal stations had mean pCO2 levels of 1182 ± 672 µatm (station ‘1100 µatm’, intertidal) and subtidal stations with mean pCO2 levels of 888 ± 471 µatm (station ‘900 µatm’, subtidal) and 714 ± 20 µatm (stations ‘700 µatm’, subtidal) (Figs 1, S1 and S2; Table 1). At stations with mean pCO2 levels of 419 ± 82 µatm (station ‘400 µatm’, intertidal) in the intertidal and 460 ± 40 µatm in the subtidal (stations ‘400 µatm’) variability in ocean acidification conditions was lower, which corresponded to a mean ΩA of 2.49 ± 0.35 intertidally and 2.23 ± 0.31 subtidally. Stations far from the seeps, had stable levels of pCO2 with 299 ± 51 µatm station ‘300 µatm’, intertidal) and 342 ± 26 µatm station ‘300 µatm’, subtidal), where the mean ΩA recorded were 3.27 ± 0.37 and 2.75 ± 0.14, respectively (Fig. 1; Table 1). Monitoring of the subtidal pH and temperature for over a month-period showed an average mean pHT of 8.14 ± 0.06 at a subtidal ‘300 µatm’ station and an average mean pHT of 7.79 ± 0.10 at the subtidal ‘900 µatm’ station (Figs 2 and S3). The ‘300 µatm’, ‘400 µatm’ and ‘900 µatm’ (‘1100 µatm’) stations represent near pre-industrial, present-day, and end of century conditions, respectively. Abiotic parameters such as dissolved oxygen, total alkalinity and depth did not differ across sites. The detailed carbonate chemistry of the surface and subtidal waters is presented in Table 1. Continuous measurements of seawater chemistry for long periods of time at stations marked with “*” in Fig. 1 are presented in Figs 2, S1, S2 and S3.

Figure 2
Figure 2

Variation of temperature and pH (total scale) over the month of June 2016 at a subtidal control site (‘300 µatm’) and a subtidal elevated CO2 site (‘900 µatm’). Measurements were carried out with the SeaFETs sensors deployed just above the seafloor.

Table 1 Carbonate chemistry in subtidal and intertidal waters off Shikine Island, Japan.

Intertidal communities

The rocky shores of Shikine Island were characterised by thick biogenic carbonate crusts formed by coralline algae, serpulids, barnacles and molluscs with an overgrowth of fleshy algae on the low shore in the intertidal zone. There was a significant difference in the abundance of macroflora and encrusting macrofauna between the different CO2 levels (Figs 3 and 4). One of the most notable shifts in community composition was a very clear decrease in the coralline algae as CO2 levels increased; this cover fell from 43 ± 21% at ‘300 µatm’ to 24 ± 21% at 400 µatm, 3 ± 5% ‘1100 µatm’ and 1 ± 2% at ‘1800 µatm’, respectively (K-W: H = 99.21, p < 0.001; Figs 3 and 4a). There was also a significant decrease in sponge cover as CO2 levels increased (K-W: H = 19.27, p < 0.001; Fig. S4). Despite reductions in coralline algae and sponges, the amount of rock covered solely by biofilm remained low throughout the CO2 gradient, with 2 ± 6% at ‘300 µatm’, 4 ± 6% at ‘1100 µatm’ and 1 ± 2% at ‘1800 µatm’ CO2 (K-W: H = 11.46, p < 0.01; Fig. S4). Fleshy algae increased in abundance from 53 ± 21% at ‘300 µatm’ to 98 ± 3% at ‘1800 µatm’ (K-W: H = 47.57, p < 0.001; Fig. 3c), and non-calcareous encrusting algae increased from 4 ± 7% at ‘300 µatm’ to 18 ± 27% and 11 ± 27%, at ‘1100 µatm’ and ‘1800 µatm’, respectively (K-W: H = 16.77, p < 0.001; Fig. S4).

Figure 3
Figure 3

Representative ecological communities at increasing pCO2 levels. The top panels represent intertidal communities associated with mean levels of 300, 400 and 1100 µatm pCO2. The bottom panels represent subtidal communities associated with mean levels of 300, 400 and 900 µatm pCO2.

Figure 4
Figure 4

Changes in abundance (mean ± SE) of taxa (mean ± SE) with increasing pCO2 for the intertidal habitat. (a) Hard corals. (b) Coralline algae. (c) Fleshy algae. (d) Calcified fauna. A significant difference between pCO2 groups is indicated with a different letter (Kruskal-Wallis with Bonferroni-adjusted Fisher’s least significant difference).

Most of the macrofauna investigated showed significant changes in abundance along the gradients in CO2. The abundance of calcifying organisms decreased as pCO2 levels rose with a significant difference between the ‘300 µatm’ and ‘400 µatm’ versus the ‘1100 µatm’ and ‘1800 µatm’, with the number of individuals falling from 38 ± 38 individuals at ‘300 µatm’ to 2 ± 3 individuals at ‘1800 µatm’ (K-W: H = 63.73, p < 0.001; Figs 3 and 4d). The abundance of the larger barnacles (>1 cm in diameter including Megabalanus volcano and Megabalanus rosa) fell from 18 ± 24 at ‘300 µatm’, 15 ± 8 at ‘400 µatm’ and 5 ± 10 individuals per 0.25 m2 at ‘1100 µatm’, and they were almost absent at ‘1800 µatm’ (K-W: H = 33.42, p < 0.001; Fig. S4). Mussels were also reduced in abundance from 7 ± 13 individuals at ‘300 µatm’ to 2 ± 3 individuals in the ‘1800 µatm’ (K-W: H = 20.80, p < 0.001; Fig. S4). Oysters and decapods were less common at the elevated CO2 stations but our surveys did not reveal statistically significant differences (K-W, p > 0.05) as they were not very abundant in quadrats at ‘300 µatm’ (Fig. S4). The azooxanthellate coral Tubastrea coccinea was observed at ‘300 µatm’ and ‘400 µatm’ but absent at ‘1100 µatm’ and ‘1800 µatm’ pCO2 (K-W: H = 14.32, p < 0.05; Fig. S4). Of the non-calcifying fauna, only sea anemones significantly increased in abundance at ‘1100 µatm’ (0.1 ± 0.4 individuals per 0.25 m2 at 300 µatm vs. 1.0 ± 1.4 at ‘1100 µatm’), they were absent from the ‘1500 µatm’ station (K-W: H = 53.89, p < 0.001; Fig. S4).

Intertidal habitat complexity was provided by barnacles, mussels and oysters, and coralline algae (which formed a thick crust) at ‘300 µatm’. These calcifying groups drastically decreased in abundance with an overall shift in the communities as pCO2 levels rose (Figs 3 and 5b). These shifts lead to a decrease in the complexity of the habitat (K-W: H = 48.50, p < 0.001), reducing two-fold from ‘300 µatm’ to ‘1100 µatm’, and more than 6-fold to ‘1800 µatm’ (Fig. 5a). At the high CO2 levels, the main habitat was low-profile fleshy algae (Figs 3 and 5a).

Figure 5
Figure 5

Changes in habitat complexity (mean ± SE), communities, and species richness with increasing pCO2 for intertidal (ac) and subtidal (df) habitats. (a,d) A significant difference between pCO2 groups is indicated with a different letter (Kruskal-Wallis with Bonferroni-adjusted Fisher’s least significant difference). (b,e) The change in communities are illustrated by an nMDS plot based on Bray Curtis distance. The colour of each point represents the pCO2: green: ‘300 µatm’, black: ‘400 µatm’, light blue: ‘1100 µatm’ and orange: ‘1800 µatm’ for the intertidal and green: ‘300 µatm’, black: ‘400 µatm’, blue: ‘700 µatm’, red: ‘900 µatm’ and pink: ‘1500 µatm’ for the subtidal. Ellipses represent the 95% interval confidence. (c,f) Algal (blue) and faunal (red) species richness are shown with darker colours used for species only found in that site, and lighter shades for species that overlap across two sites. For the subtidal, the species overlap are graduated (from darkest to lightest) in the following order: 300–400 µatm, 300–900 µatm and 400–900 µatm (no species were common to all three sites).

Despite the increasing abundance of fleshy algae with rising pCO2, there was a 56% reduction in algal species richness from ‘300 µatm’ (18 spp.) to ‘1100 µatm’ (8 spp.) with little overlap in species composition between these two CO2 levels (Fig. 5c and Table S1). The ‘300 µatm’ stations had a diverse community of Rhodophyta with 16 species compared to only six species at ‘1100 µatm’. There were 33 and 32 macrofaunal taxa at ‘300 µatm’ and ‘1100 µatm’ respectively, but the community composition was very different, with only seven species common to both sets of stations (Fig. 5c and Table S1).

Subtidal zone

Changes in the subtidal benthic community were remarkably similar to those observed intertidally, with reduced abundances of calcifying organisms as CO2 levels increased from ‘300 µatm’ to ‘400 µatm’ and again to ‘700 µatm’ and beyond (Figs 3 and 6). The cover of coralline algae (K-W: H = 42.46, p < 0.001; Fig. 6b) and hard corals (K-W: H = 19.67, p < 0.001; Fig. 6a) was significantly reduced as CO2 levels rose. Hard corals were common at ‘300 µatm’, where they had 11 ± 22% cover, however, they were only sporadically found at ‘400 µatm’ with just two colonies observed accounting for 0.7 ± 1.6% cover, and absent from more highly elevated CO2 stations (Figs 3 and 6a). Soft corals and anemones were not recorded in the elevated CO2 stations corresponding to the end-of-the-century projections (‘700 µatm’, ‘900 µatm’ and ‘1500 µatm’) and were rare at ‘300 µatm’ and ‘400 µatm’. Due to their low abundance at ‘300 µatm’ and ‘400 µatm’, the soft corals and the anemones did not significantly differ with CO2 level (K-W: H = 6.32, p = 0.18 and H = 5.09, p = 0.27 respectively) (Fig. S4).

Figure 6
Figure 6

Changes in abundance (mean ± SE) of taxa with increasing pCO2 for the subtidal habitat. (a) Hard corals. (b) Coralline algae. (c) Canopy-forming fleshy algae. (d) Turf algae. (e) Low-profile fleshy algae. (f) Non-calcified encrusting algae. A significant difference between pCO2 groups is indicated with a different letter (Kruskal-Wallis with Bonferroni-adjusted Fisher’s least significant difference).

The cover of non-calcifying macroalgae was high at all subtidal stations yet there were major shifts in community composition (Figs 3 and 6c–f). Large canopy forming macroalgae had significantly reduced abundance at ‘400 µatm’ and higher pCO2 end-of-the century projections (K-W: H = 18.53, p < 0.001, Fig. 6c) whereas low-profile algae and turf algae increased in cover as CO2 levels rose, with their cover significantly higher at ‘400 µatm’ and higher CO2 level stations compared to ‘300 µatm’ stations (K-W: H = 23.41, p < 0.001 and H = 44.81, p < 0.001 Fig. 6d,e). Due to the overall reduction in the percentage of calcified and non-calcifying macroalgae, the proportion of biofilm encrusted substrata significantly increased from 2 ± 3% to 20 ± 14% at ‘300 µatm’ and ‘1500 µatm’ respectively (K-W: H = 32.88, p < 0.001; Fig. S5).

Both hard corals and canopy forming macroalgae formed a biogenically complex habitat in the subtidal zone at ‘300 µatm’ CO2 (Fig. 3). The sharp decrease of these two groups lead to significantly reduced habitat complexity (K-W: H = 50.48, p < 0.001) at CO2 levels corresponding to the mid- (‘400 µatm’) and end-of-the-century projections (‘700 µatm’, ‘900 µatm’ and ‘1500 µatm’) (Figs 3 and 5c). The communities radically changed as pCO2 rose with distinct communities observed at each pCO2 site (Fig. 5d) with less complex low-profile and turf algae dominating at the highest pCO2 (Fig. 3).

The species richness of the benthic flora and fauna was reduced by 71% as CO2 levels rose, with a total of 49, 20 and 14 species at ‘300 µatm’, ‘400 µatm’ and ‘900 µatm’, respectively (Fig. 5f and Table S2). This change in faunal species richness included seven hard coral species, a sea anemone, a soft coral species and a sponge, which were only observed at ‘300 µatm’. In addition, small gastropods were abundant at ‘300 µatm’, but not at ‘400 µatm’ or ‘900 µatm’. Other mobile benthic fauna that were only found in the ‘300 µatm’ stations were sea cucumbers and coral boring serpulids and barnacles. Algal diversity was greatly reduced shifting from a diverse community with 22 species at ‘300 µatm’ to only 10 species at both the ‘400 µatm’ and ‘900 µatm’ stations, with only four species overlapping in species composition between ‘400 µatm’ and ‘900 µatm’ (Fig. 5f and Table S2). This is an underestimate of algal diversity as crustose coralline algae were counted as one taxon and most turf or very low-profile algae were not included, exceptions were larger algae such as Lobophora variegata and Caulerpa chemnitzia var. peltata. At ‘900 µatm’, the only abundant canopy forming macroalgae was the red algae Grateloupia elata (Table S2).

Discussion

Our comparisons of intertidal and subtidal rocky reef communities along natural gradients in CO2 have revealed that ocean acidification is a threat to many marine organisms, as it can drive fundamental shifts in coastal marine ecosystems towards simplified, low diversity communities. Abrupt changes in subtidal and intertidal communities were revealed from present-day to near-future levels of CO2 (300 µatm to 400 µatm), and then again to future levels (400 µatm to 700 µatm) and beyond. In natural coastal ecosystems, mean pCO2 levels predicted for as soon as the mid-century will have periods of such low aragonite saturation and high availability of inorganic carbon that this will cause biodiversity loss driven by a decline in habitat-forming species (e.g. coralline algae, canopy-forming macroalgae, scleractinian corals, and barnacles) and an increase in low-profile and turf algae. Our observations suggest that ocean acidification will shift ecosystems at subtropical−temperate transition zones from complex calcified biogenic habitats towards less complex non-calcified habitats.

Increases in dissolved CO2 provide a resource for algae that cannot use bicarbonate ions for their photosynthesis37 and is expected to increase the prevalence of macroalgae8,9,12,38. The significantly increased occurrence of low-profile fleshy algae with increasing pCO2 aligns with results from other shallow marine carbon dioxide seeps. However, not all macroalgae species respond in the same manner to the effects of elevated CO2, with some species gaining a relative advantage over their counterparts3. The resulting pattern is that ocean acidification alters successional development due to competition for space by a few highly tolerant species39,40. The prevalence of low-profile fleshy algae in our elevated pCO2 sites may contribute towards the observed decline in canopy-forming macroalgae and corals41. In this context, natural analogues offer opportunities to assess competitive interactions and the effects of ocean acidification on ecological functions40.

The presence of highly calcified communities at all of our reference sites reflects the high carbonate saturation levels that typify this region due to naturally low background pCO2 levels20. At the highest CO2 stations the exposed shells and skeletons of calcifying organisms had visible signs of dissolution, as seen in other field studies worldwide42,43,44,45. The decrease in the abundance of calcifying macrofauna from our reference sites to ‘400 µatm’ sites, where even the lowest Ωaragonite remains higher than values typically observed nowadays in many parts of the ocean46,47, suggests that ocean acidification is already impairing the growth and survival of calcifiers19. This is a concern and provides an insight into the effects of ocean acidification in other parts of the world that have already experienced increases in pCO2 from 300 µatm to 400 µatm during the last century since the Industrial Revolution.

Communities of zooxanthellate scleractinian corals currently thrive at high latitude (here 34° N) in East Asia due to warm, northward flowing currents which bring low pCO2, high carbonate saturated waters into the region48. These communities are an important reservoir of diversity for hermatypic corals, and a number of species found at our study site are endemic to the region49. We observed an abrupt decline in their abundance and diversity as CO2 levels rose and CaCO3 saturation state fell. Despite differences in biogeography, the major ecosystem changes we recorded along the CO2 gradients are broadly consistent with findings from other naturally acidified tropical coral reef settings12,13,50. Moreover, these patterns are comparable to those seen on tropical reefs in Florida, where present-day seasonal reductions in saturation state are contributing to reef dissolution, the die-back of scleractinians and an increase in low-profile fleshy algal growth44,51.

The Japanese subtropical-temperate transition zone is highly diverse due to a mix of subtropical and temperate species, which allows for the coexistence of diverse macroalgae with scleractinian zooxanthellate corals. This zone is at the leading-edge for subtropical species and the trailing-edge for temperate species, and this biogeographic boundary is likely to undergo fundamental shifts with future climate change52,53. With increased temperature threatening corals in the tropics54, it could be expected that higher latitudes will act as refugia, but this would require the loss of other ecologically important species that typically dominate these latitudes55. Our results support the notion that ocean acidification may constrain the shift of coral to higher latitudes56,57,58.

Biogenic complexity promotes the provisioning of habitats, allowing high levels of biodiversity to be sustained within an ecosystem5. Reductions in habitat complexity cause a reduction in biodiversity5,59. We found that as CO2 levels rose, there was a shift from structurally complex canopy-forming fleshy algae and corals to less complex low-profile fleshy algae and an absence of corals. This reduction in habitat complexity may have contributed towards the reduced species richness in our elevated pCO2 sites, as well as the minimal overlap in observed species among the different sites as many marine organisms rely on a particular habitat (e.g. ref.60). As the effect of ocean acidification could cause a simplification of the ecosystems, we can expect ocean acidification to also alter the delivery and the quality of the ecosystem services associated with these marine communities61 and this should be a focus of future work.

Carbon dioxide seeps are open systems that allow recruitment from outside and this hinders genetic adaptation62. Whilst organisms that survive at such seeps may upregulate genes to acclimate to high pCO2 levels63, only species with very limited genetic dispersal can be expected to evolve to cope with the local conditions64. The CO2 seep systems described in this report can nevertheless provide insights into how marine ecosystems have been changing under increased anthropogenic CO2 and into the near future. Thus, reference sites showed pre-industrial levels of CO2 and sites on the fringe of the CO2 gradient showed present-day and mid-century CO2 levels with minimum variations of these levels on short periods of time. Extreme variations of pCO2 concentrations at natural analogues are commonly observed11,13 and may bias the observed response of organisms65. Such extreme variations in pCO2 levels were also observed at the highest pCO2 sites of the Shikine CO2 systems, yet we also located stations with small increases and variations in pCO2 that are well suited to projected levels of ocean acidification.

In conclusion, we found that an increase in CO2 resulted in profound community-level changes in a biodiverse subtropical-temperate transition zone. Both intertidal and subtidal communities became highly simplified, with reduced biogenic habitat complexity and biodiversity. We highlight that ocean acidification may constrain tropical coral range expansion. Our findings suggest that a threshold for macroalgal and coral habitats at the subtropical-temperate transition zone is likely to be exceeded by 2050, with even more extreme changes expected by the end-of-the-century. Overall, ocean acidification is expected to simplify coastal marine communities throughout East Asia.

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Acknowledgements

The authors would like to thank the technical staff of Shimoda Marine Research Center, University of Tsukuba for field assistance and Prof. Hiroyuki Fujimura, University of the Ryukyus, for total alkalinity measurements. This research was part of the ‘Japanese Association of Marine Biology’ project. This study was partially supported by the ‘International Educational and Research Program’, University of Tsukuba. Travel costs were funded the Daiwa Foundation (Grant Number: 10777/11517) for J.M.H.-S., and by a Japan Society for the Promotion of Science Short Term Invitation Fellowship (Grant Number: S16073) for M.M.

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Affiliations

  1. Shimoda Marine Research Center, University of Tsukuba, 5-10-1 Shimoda, Shizuoka, 415-0025, Japan

    • Sylvain Agostini
    • , Ben P. Harvey
    • , Shigeki Wada
    • , Koetsu Kon
    • , Kazuo Inaba
    •  & Jason M. Hall-Spencer
  2. Dipartimento di Scienze della Terra e del Mare, University of Palermo, CoNISMa, via Archirafi 28, 90123, Palermo, Italy

    • Marco Milazzo
  3. Marine Biology and Ecology Research Centre, University of Plymouth, Plymouth, PL4 8AA, UK

    • Jason M. Hall-Spencer

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Contributions

S.A., B.P.H. and J.M.H.-S. wrote the manuscript. S.A., S.W., K.K., M.M. and J.M.H.-S. designed and conducted the surveys. S.A., B.H., S.W., K.K. and K.I. analyzed the data. All authors contributed substantially to revisions.

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The authors declare no competing interests.

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Correspondence to Sylvain Agostini.

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