Warming and changes in ocean carbonate chemistry alter marine coastal ecosystems at an accelerating pace. The interaction between these stressors has been the subject of recent studies on reef organisms such as corals, bryozoa, molluscs, and crustose coralline algae. Here we investigated the combined effects of elevated sea surface temperatures and pCO2 on two species of photosymbiont-bearing coral reef Foraminifera: Heterostegina depressa (hosting diatoms) and Marginopora vertebralis (hosting dinoflagellates). The effects of single and combined stressors were studied by monitoring survivorship, growth, and physiological parameters, such as respiration, photochemistry (pulse amplitude modulation fluorometry and oxygen production), and chl a content. Specimens were exposed in flow-through aquaria for up to seven weeks to combinations of two pCO2 (~790 and ~490 µatm) and two temperature (28 and 31 °C) regimes. Elevated temperature had negative effects on the physiology of both species. Elevated pCO2 had negative effects on growth and apparent photosynthetic rate in H.depressa but a positive effect on effective quantum yield. With increasing pCO2, chl a content decreased in H. depressa and increased in M. vertebralis. The strongest stress responses were observed when the two stressors acted in combination. An interaction term was statistically significant in half of the measured parameters. Further exploration revealed that 75 % of these cases showed a synergistic (= larger than additive) interaction between the two stressors. These results indicate that negative physiological effects on photosymbiont-bearing coral reef Foraminifera are likely to be stronger under simultaneous acidification and temperature rise than what would be expected from the effect of each of the stressors individually.
Coral reef ecosystems react sensitively to rapid climatic events and changes in ocean carbonate chemistry (Hoegh-Guldberg et al. 2007; Wernberg et al. 2013). It is increasingly acknowledged that an understanding of the effect of these stressors on marine organisms requires experiments investigating the combined effects of multiple stressors. In theory, when the stressors individually have a negative effect, then their combined effect can be either additive (total effect C = A + B), antagonistic (C < A + B), or synergistic (C > A + B) (Crain et al. 2008). In the context of global change, it is especially important to understand whether synergistic effects are likely to occur under the combination of stressors. Interactive effects of warming and rising pCO2 have been observed in marine organisms, such as corals, bryozoa, molluscs, and crustose coralline algae (Reynaud et al. 2003; Anthony et al. 2008; Rodolfo-Metalpa et al. 2010, 2011). A meta-analysis of a decade of climate change experiments on marine organisms indicated that environmental stressors can have significant combined effects, often not detectable in single-stressor studies (Wernberg et al. 2012). The negative effects of raised pCO2 are amplified by simultaneously elevated temperatures in marine crustose coralline algae and macroalgae, but indicate that the response to the combined treatment is species specific (Martin and Gattuso 2009; Koch et al. 2013). In contrast, McCulloch et al. (2012) showed that increasing temperature may counteract the negative effects of acidification on calcification in corals, by facilitating upregulation of pH at the site of calcification. Collectively, these studies illustrate that coral reef organisms exhibit significant interactive effects in response to key global change stressors, but the strength and direction of response differ among taxa.
Pörtner (2002, 2008) argued that protists and especially prokaryotes might be less vulnerable to pCO2 and temperature stress than more complex macro-organisms because the latter are more specialised on a molecular level. An ecologically significant group of protists on coral reefs are benthic Foraminifera. Foraminifera are major ecosystem engineers in coral reefs because they contribute significantly to the carbonate sediment production (Langer et al. 1997), providing substrata for other coral reef organisms. Larger Foraminifera host photosymbionts, which facilitate growth to cell sizes 10–100 times larger than their asymbiotic relatives (Hallock 1985; Lee and Hallock 1987; Lee 1995). The endosymbiosis is sensitive to thermal and light stress, leading to bleaching analogous to that in corals (Hallock et al. 1992; Hallock and Talge 1993). The effect of thermal stress in Foraminifera has been documented in laboratory studies (Talge and Hallock 2003; Schmidt et al. 2011; Uthicke et al. 2011). In the field, thermal pollution was documented to effect foraminiferal species composition (Arieli et al. 2011).
The effect of changes in ocean carbonate chemistry on Foraminifera due to raised pCO2 levels in the atmosphere is not yet fully understood. Experimental manipulations of various species of Foraminifera using pCO2 levels of up to 2,000 μatm have shown no evidence for reduced survivorship (McIntyre-Wressnig et al. 2013), nor any effects on photobiology and calcification (Vogel and Uthicke 2012), supporting the hypothesis of Pörtner (2002, 2008). Other studies, however, have shown reduced calcification of coral reef Foraminifera at elevated pCO2 levels (Kuroyanagi et al. 2009; Haynert et al. 2011; Reymond et al. 2013). Fujita et al. (2011) reported that calcification in two tropical Foraminifera hosting diatoms and exhibiting a hyaline shell increased with elevated pCO2 up to 770 µatm and decreased at pCO2 levels up to 970 µatm. One species with a porcelaneous shell decreased in size with increasing pCO2. Species-specific responses have been confirmed in a study by Hikami et al. (2011). Studies of Foraminifera from natural CO2 seeps with locally decreased pH reported increasing incidences of altered shell structure, decreasing population densities, declining diversity in calcifying Foraminifera, and increasing proportion of Foraminifera with agglutinated shells towards low pH/high pCO2 (Dias et al. 2010; Fabricius et al. 2011; Uthicke and Fabricius 2012; Uthicke et al. 2013). Test dissolution has been reported under elevated pCO2 (Sinutok et al. 2011).
Interactive effects of elevated pCO2 and eutrophication have been shown to impact growth in Marginopora rossi (Reymond et al. 2013). Elevated temperatures and eutrophication can also have interactive negative effects on growth and survivorship in Marginopora vertebralis (Uthicke et al. 2011). Negative effects of elevated temperatures are more severe in the presence of low concentrations of the herbicide Diuron (van Dam et al. 2012).
The main aim of this study was to investigate the individual effects of pCO2 and temperature and their combined effects on coral reef Foraminifera. In particular, we aimed to gain a better understanding of parameters targeting the foraminiferal photosymbionts (photosynthesis, oxygen production, and chl a content) and the holobiont (survivorship, respiration, and growth) in response to a combination of stressors. The multi-factorial experiment consisted of two pCO2 levels (pH 7.9 and 8.1) and two temperature levels (28 and 31 °C). The elevated treatments (31 °C and pH 7.9) simulate levels that are predicted to occur by the end of the century in Australian coastal waters (Lough and Hobday 2011; Redondo-Rodriguez et al. 2012). Since investigations of multiple stressors on other marine organisms showed significant differences among taxa, the experiment included two species of Foraminifera. Heterostegina depressa and M. vertebralis represent two phylogenetically distinct clades that appear to have diverged >500 million years ago, evolved calcification independently of each other (Pawlowski et al. 2003) and host different types of photosymbionts (Lee 2006).
Materials and methods
Species selection and sample collection
Two species of Foraminifera were investigated: M. vertebralis and H. depressa. M. vertebralis represents the family Soritidae, which produces imperforate, porcelaneous tests made of high-Mg calcite (Blackmon and Todd 1959). This species is abundant in shallow reef settings of the Indo-Pacific Ocean (Langer and Lipps 2003). It harbours dinoflagellate symbionts of the genus Symbiodinium (Pochon et al. 2007; Momigliano and Uthicke 2013). H. depressa is a representative of the family Nummulitidae, which produces multi-layered, perforate low Mg-calcite tests and harbours endosymbiotic diatoms (Lee et al. 1980; Leutenegger 1984). This species occurs in highest abundance below 10-m water depth and is less abundant in highly energetic shallow habitats (Hohenegger et al. 1999; Renema 2006; Nobes et al. 2008). Specimens were collected from Orpheus Island in the central Great Barrier Reef in September 2011. H. depressa was collected at a depth of 8–12 m from coral rubble (Cattle Bay, 18°34′08″S 146°28′55″E) and M. vertebralis at a depth of 0–1 m (below Lowest Astronomical Tide) from turf algae-covered rocks (Hazard Bay, 18°38′58″S 146°29′11″E). Both species were acclimated to laboratory conditions in tanks with moderate flow-through conditions (same as used in experimental setup) under low-light conditions (10 µmol photons m−2 s−1) for a period of 3 weeks.
Experimental design and carbonate system parameters
12 flow-through aquaria (working volume 17.5 L) were installed in a constant temperature room, and the experiment was carried out over a period of 53 d. The duration of experimental exposure was adapted to the species’ biological response in order to perform final respiration and production measurements on all treatments. The exposure time of 53 d for M. vertebralis and 35 d for H. depressa was deemed adequate to observe the effects of long-term stress. For each temperature (28 and 31 °C) and pCO2 level (~790 µatm, pHNIST 7.9 and ~490 µatm, pHNIST 8.1), three replicate tanks were used; replicate tanks were randomly allocated to treatments. Seawater was pumped from the ocean into the laboratory, filtered to 5 µm, and stored in four header tanks where it was modified to the desired experimental conditions. Temperature was manipulated through a computer-controlled data logger (CR 1000, Campbell Scientific, Australia). Titanium heating rods in the four header tanks heated the incoming seawater to the set temperatures, which were monitored by the data logger in each header tank and in one aquarium per treatment. The seawater was then pumped into the aquaria at a flow rate of 450–500 mL min−1 (determined by flow indicators, RS Components, Ltd., UK). Manual temperature and pH measurements were performed once to twice per day (Table 1), using a Eutech, USA, probe and Oakton, USA, console. For the increased pCO2 treatment, water chemistry was manipulated by bubbling analytical CO2 into the header tanks. The water chemistry was controlled by a computer aquarium system (Aquamedic, Germany), as described in Uthicke et al. (2011) and Vogel and Uthicke (2012). Water samples for total alkalinity (A T) and dissolved inorganic carbon (DIC) determinations were taken weekly and analysed by AIMS Laboratory Services (Vindta 3C). The program CO2 SYSCALC.EXE (Lewis and Wallace 1997) was used to calculate carbonate system parameters from A T, DIC, salinity, and temperature values (Table 1).
Experimental approach mimicking ‘natural’ conditions
Specimens were kept inside custom made flow-through housings in each aquarium to achieve higher flow conditions more closely mimicking their habitat than in previous experiments (Schmidt et al. 2011; Uthicke et al. 2011; Vogel and Uthicke 2012). Flow-through housings contained two levels made from two standard 6-well cell-culturing plates with flow-through lids (Electronic Supplementary Material, ESM Fig. S1). Twenty-four specimens (four specimens per well) of H. depressa were put in the lower level and the same number of M. vertebralis in the top level. Foraminifera were contained in the housings by placing a plankton mesh (Ø 0.5 mm: H. depressa, Ø 1 mm: M. vertebralis) and additional shading cloth between plate and lid, held tight by rubber bands (ESM Fig. S2). For the construction of the housings, six larger circles (Ø 3.5 cm) were cut into the lids as water outlets and six smaller circles (Ø 0.3 cm) on each side as water inlets. Black plastic tubing was used to space the plates 1 cm apart and to connect them horizontally and vertically. At the top end, a small aquarium pump delivered a constant flow of water from the aquarium to the inside of the housings. Flow into each well was visible because small flow indicators (1-cm-long red ribbons glued at one end inside each inlet of the housings) were constantly held in place by the flowing water. Flow rates into the individual wells were recorded before and after the experiment, ranging between 180 and 220 mL min−1. Velocity of the water flow varied from 4.2–5.2 × 10−1 m s−1 at the inlet (Ø 0.3 cm) to 3.1–3.8 × 10−3 m s−1 at the outlet (Ø 3.5 cm). The flow rates between inlet and outlet are in the same range as those measured in situ over dead coral rubble (Williams and Carpenter 1998) and sea grass (Cornelisen and Thomas 2009). Both species kept in the flow-through housings appeared to thrive as indicated by healthy colouration, minimal shell breakage, and the development of firm attachment to the walls of the housings by the pseudopodial network. H. depressa was attached to the walls of the housings, whereas M. vertebralis was attached to the flat bottom of the housings, mimicking its firm attachment and its natural position on sea grass leaves. The flow-through system had the disadvantage that a small number of specimens were lost during the experiment (mean specimen loss per treatment: H. depressa: 5–13 %, SD = 0–10 %; M. vertebralis 0–6 %, SD = 0–7 %).
Experimental light levels
Flow-through housings were made containing two levels so that one species could be kept in the top level exposed to higher light levels than the species in the lower level. Light levels were chosen for each species separately because of their known distributions and different light saturation points determined by pulse amplitude modulation (PAM) fluorometry (Hohenegger 2004; Ziegler and Uthicke 2011; Vogel and Uthicke 2012). PAM fluorometry results for M. vertebralis indicated a maximum saturating irradiance (E k) between 100 and 140 µmol photons m−2 s−1 and for H. depressa between 40 and 60 µmol photons m−2 s−1 (Ziegler and Uthicke 2011). The light levels used in the experiment were chosen to fall below the E k values by Ziegler and Uthicke (2011) and P–I curve P max values determined by Vogel and Uthicke (2012) and were selected to correspond to levels which have shown no changes in mortality rates or chlorophyll a concentrations in previous experimental manipulations of the studied species (Schmidt et al. 2011; Uthicke et al. 2011; Vogel and Uthicke 2012; Reymond et al. 2013). H. depressa was put in the lower level (10–17 µmol photons m−2 s−1) of the flow-through housings and M. vertebralis in the top level (38–45 µmol photons m−2 s−1) because the latter has a higher E k point, compared with the diatom-bearing species (Ziegler and Uthicke 2011). Overall, light levels inside the tanks (140–150 µmol photons m−2 s−1) were recorded at the beginning and the end of the experiment using a light quantum sensor (Apogee MQ-200, USA). Light was supplied by 50:50 actinic 420 nm/10 K trichromatic daylight fluorescent grow tubes (Catalina Compact, 12-h dark/12-h light cycle). Green shade cloth (light reduction by ~30 %) was used for M. vertebralis, and black shade cloth (light reduction by ~50 %) was used for H. depressa. Shade cloth and plankton mesh were exchanged every week to keep light levels constant over the experimental period.
Survivorship and growth
To determine % survivorship, specimens were examined twice per week and recorded as living, when their cytoplasm exhibited colour, or dead, when the shells and cytoplasm were pale and no cytoplasmic activity was observed (Bernhard 2000). Growth of H. depressa and M. vertebralis was expressed as the increase in cross-sectional surface area per day over the experimental period. Procedures of high-resolution photography before and at the end of the experiment were the same as previously published (Uthicke and Altenrath 2010; Schmidt et al. 2011; Vogel and Uthicke 2012). Surface area (mm2) of individual Foraminifera was measured and analysed as described in Schmidt et al. (2011). H. depressa growth rates have been based on tracking individuals within one well from the beginning to the end of the experiment. This was possible by following distinct shell features and overall size among the images through time. M. vertebralis growth rates had to be based on overall means of wells because the shells of this species do not possess characteristic differences that would allow the tracking of individual specimens. Wells where M. vertebralis were lost were excluded from the data set, as were wells where mechanical damage to the specimens occurred. Growth rates (% d−1) were determined following the equation of ter Kuile and Erez (1984). Average initial surface area of analysed specimens did not deviate between treatments both with respect to the mean values and the variance (H. depressa: one-way ANOVA, F 1,143 = 0.29, p = 0.8346; Levene’s Test, F 3,142 = 1.22, p = 0.304; M. vertebralis: one-way ANOVA, F 1,57 = 1.10, p = 0.3559; Levene’s Test, F 3,53 = 1.077, p = 0.366).
Photobiology, oxygen consumption, and chlorophyll a concentration
Photochemical performance of Photosystem II (PSII) was measured by obtaining the maximum quantum yield (MQY, dark adapted yield, F v:F m) and the effective quantum yield (EQY, light adapted yield, ΦPSII) of individual H. depressa and M. vertebralis before and at the end of the experiment with an Imaging-PAM Fluorometer (WALZ, Unit IMAG-CM, Maxi Head, Germany; Schmidt et al. 2011; Uthicke et al. 2011; Vogel and Uthicke 2012). Foraminifera were transferred into 6-well plates containing the respective treatment water and dark adapted for 20 min prior to measuring MQY. Similar light conditions as in the aquaria, supplied by the LED unit of the Maxi head (H. depressa, 10–14 µmol photons m2 s−1, M. vertebralis 35–40 µmol photons m2 s−1), were used to measure EQY. Calculations of EQY (ΦPSII) and MQY (F v:F m) were conducted by the software Imaging Win (WALZ, Germany) after independent AOI (Areas of Interest) were put on the individual Foraminifera from which the measurements were read. For further information on the Imaging-PAM, details are described in Hill et al. (2004). Additionally, PAR-absorptivity (Abs) was measured as the ratio of reflectance of red light (650 nm, R) to the reflectance of non-absorbed near-infrared light (780 nm, NIR) from individual Foraminifera at the end of the experiment. This is based on the assumption that the change in photosynthetic pigments within the same species will alter the absorption of red light and change the ratio. For calculating the apparent photosynthetic rate (APR, Ps), we used the formula: Abs × EQY × light intensity (Cooper and Ulstrup 2009). Absorptance measurements are used to calculate APR and are influenced by differences in the calcareous shells of the species. Therefore, affecting absolute and relative differences and are thus only discussed in light of relative changes in response to the tested environmental parameter and not used to compare absolute values between the species.
Respiration and photosynthesis rates were determined in incubation chambers by measuring changes in oxygen concentration during a 15-min dark phase followed by a 15-min light phase, using a custom-build respirometer (Uthicke et al. 2011; Vogel and Uthicke 2012), before and after the experiment. Non-invasive oxygen sensor spots (‘optodes’, Ø 5 mm) were attached to closed glass vials (volume 6.6 mL) containing the Foraminifera. Fibre optic cables connected these to an OXY-4 mini transmitter (Presens, Germany). Prior to measurements, specimens were incubated in the dark for a minimum of 25 min to stabilise temperatures in the flow-through water bath. For photosynthesis measurements, Foraminifera were exposed to the same light conditions as used in the experiment (light sources: Catalina compact: 420 nm actinic/1,000 K). In each run, one out of four vials did not contain any species, to test for potential respiration not caused by the Foraminifera. Prior to the experiment, baseline respiration and production rates were measured in the ambient pCO2 and temperature treatment. For each of these replicates, prior to and at the end of the experiment, 3 specimens of M. vertebralis and 6–8 specimens of H. depressa were pooled to obtain a sufficiently strong signal. For final measurements, five replicates were measured per aquarium for M. vertebralis and two for H. depressa. Respiration rates were normalised to wet weight (determined to 0.01 mg accuracy with balance, Mettler-Toledo), which is known to be highly correlated with dry weight in Foraminifera (Schmidt et al. 2011). Daily net production rates were calculated assuming that the respiration rates reflect a 12-h night cycle and production rates the 12-h day cycle. To determine how the observed changes in photosynthetic performance are linked with pigment content of the whole organism, the average concentration of chlorophyll a was determined at the end of the experiment for a subset (four specimens) per aquaria. Chlorophyll a was extracted and quantified following the protocol described in Schmidt et al. (2011).
For statistical analyses, MQY (F v:F m), EQY (ΦPSII), growth, and survivorship were arc sine transformed because they represent proportions or percentages. Oxygen respiration and production were log (x + 1) transformed and chl a pigment data were log transformed to meet the assumption of the ANOVA. Residual and normality plots on transformed data indicated that assumptions of equal group variance and normality were not violated. Changes in all parameters under the respective temperature and pCO2 treatments were analysed using linear models, into which average temperature and pH for each individual aquarium obtained through manual measurements were inserted as factors including their interaction term. The analysis of MQY, EQY, and APR was based on average values per well, yielding each a total of 72 values (6 wells * 4 treatments * 3 replicate tanks). Analysis of respiration parameters was based on two replicate measurements per tank for H. depressa (N = 24) and four replicate measurements per tank for M. vertebralis (N = 48). Analysis of chl a content was based on four replicate measurements per tank (4 specimen * 4 treatments * 3 replicates, N = 48). Analysis of survivorship was based on values for each of the three replicate tanks (N = 3). Analysis of growth rates was based on averages per well for H. depressa (N = 68) and for M. vertebralis (N = 57).
All analyses were conducted in Jmp, Version 10 (SAS 2012). In cases where linear models indicated significant effects in both parameters, or a significant interaction between the stressors, we calculated the expected additive inhibition from each individual parameter according to a standard ecotoxicological model (Bliss 1939) to compare observed effects with expected effects. We determined combined effects from fraction changes of the treatments compared with the control (28 °C, 479 µatm pCO2). Additivity can be presumed when both individual factors are significant, but their interaction is not. In cases where a significant interaction term is present, comparison of the predicted with the observed effect of the combined stressors can reveal if antagonism (C < A + B), or synergism is indicated (C > A + B; Crain et al. 2008).
All experimental data will be made available via www.pangaea.de.
Daily temperature and pCO2 measurements inside each aquarium are summarised in Table 1. The actual values represent closely the target values of the treatments. The aragonite (Ω Ar) and calcite (Ω Ca) saturation states in the elevated pCO2 (~790 µatm) treatment remained well saturated throughout the experiment, but clearly below that of the ‘control’ treatment.
Survivorship in H. depressa decreased significantly with temperature compared with the controls (Table 2). Survivorship did not decrease with increasing pCO2 (change of 2 %) and decreased significantly in the combined treatment by 26 % (Fig. 1). Both stressors acted synergistically on survivorship in H. depressa because proportional change compared with the controls was more than 3 times higher than the predicted additive effect (Table 3). As a result of the high survivorship in M. vertebralis, no effects of any of the treatments or their combination on survivorship were found.
Elevated temperature and pCO2 had a significant negative effect on growth in H. depressa (Table 2). Although the interaction term is not significant, it is noteworthy that the lowest growth occurred in the combined treatment (Fig. 2). In the control treatment (28 °C, pH 8.1), H. depressa grew on average at 0.39 % mm2 d−1 which is a factor of five higher than growth rates of M. vertebralis, which grew on average at 0.07 % mm2 d−1. Elevated temperature and pCO2 alone had no significant effect on growth in M. vertebralis but the interaction term was significant (Table 2). The most likely cause for the interaction is a strong increase in growth under elevated pCO2 at 28 °C (49 %) whereas all other treatments were similar to the controls.
In H. depressa, temperature had a significant negative effect on all of the photophysiological parameters measured (Fig. 3a–f; Table 2), whereas elevated pCO2 had a significant negative effect on APR and a significant positive effect on EQY. In M. vertebralis temperature had a significant negative effect on all three photophysiological parameters whilst elevated pCO2 had no significant effect on either parameter. Significant interactive effects of the treatments have been found in MQY and EQY for H. depressa and in EQY for M. vertebralis (Table 2). The combined effect of the two stressors on EQY was antagonistic, because the observed inhibition in the combined treatment was lower that the predicted combined inhibition.
For both species, daily average net oxygen production rates were positive in all treatments ranging from 0.03 to 0.05 µg O2 h−1 mg−1 (Fig. 3g, h). In both species elevated temperatures reduced oxygen production more than respiration rates (µg O2 h−1 mg−1; Fig. 3g–j) whereas elevated pCO2 levels had no significant effect on production or respiration. A significant interaction of pCO2 and temperature was observed for respiration rates in M. vertebralis (Table 2). Compared with the control treatment, respiration rates in the elevated temperature treatment were reduced by 19 % and elevated by 6 % in the pCO2 treatment compared with the controls. The highest reduction in respiration rates (46 %) was observed in the combined treatment, explaining the significant interaction term and highlighting the synergistic effect of both stressors on respiration in M. vertebralis.
The chl a pigment concentration in H. depressa was significantly reduced under elevated temperatures. The interaction with pCO2 was significant as shown by a reduction in the combined treatment by 52 % compared with the controls (Fig. 4). In the elevated temperature treatment it decreased by 41 % and hardly changed (3 %) in the raised pCO2 treatment. The strongest reduction in chl a content occurred in the combined treatment, suggesting that the combined effect is synergistic. Chlorophyll a pigment content was in the same range in the control treatments before and after the experiment with initial concentrations of 0.13 (SD = 0.03) µg mg−1 wet weight and final 0.16 (SD = 0.03) µg mg−1 wet weight in H. depressa and initial 0.12 (SD = 0.008) µg mg−1 wet weight final 0.15 (SD = 0.02) µg mg−1 wet weight in M. vertebralis. This indicates that symbiont bleaching did not occur in the control treatments.
Temperature, pCO2, and their interaction had significant effects on the chl a content in M. vertebralis (Table 2). Compared with the control treatment, chl a content in the temperature treatment was reduced by 41 %. In the pCO2 treatment chl a content was elevated by 8 % compared with the controls. Despite the apparent positive effect of pCO2 alone, the highest reduction (72 %) was observed in the combined treatment, suggesting a synergistic effect of the stressors on this variable.
In summary, due to temperature elevation, 100 % of the parameters in H. depressa and 75 % of parameters in M. vertebralis were reduced compared with the controls (Table 3). Elevated pCO2 alone had a significant negative effect on 13 % of the parameters among both species but in combination with temperature, 50 % of all measured parameters showed significant negative effects (Table 3).
The strongest reductions in the studied parameters were observed in the treatments where the two stressors acted in combination. An interaction term was statistically significant in half of the measured parameters (Table 2). Of these, 75 % showed a synergistic interaction between the two stressors whereas the remaining 25 % of the interactions were antagonistic (Table 3).
Photosynthesis, respiration, and chlorophyll a content
Elevated levels of temperature had a significant effect on all photosynthetic parameters, which is consistent with results of previous studies of temperature-induced bleaching in benthic Foraminifera (Schmidt et al. 2011; Uthicke et al. 2011). Temperatures above 30 °C appear to lead to damage on the protein level in the holobiont and reduce carbon fixation rates of the symbionts due to reduced expression of the RuBisCO enzyme (Doo et al. 2012). In contrast to the strong effect of temperature, elevated levels of pCO2 had mixed influences on photosynthetic parameters (Table 3). Negative effects of elevated pCO2 on photosynthetic rates of Symbiodinium are known to occur at high pCO2 levels, but at intermediate levels, pCO2, even in combination with raised temperature, induced an increase in symbiont oxygen production in Acropora intermedia (Anthony et al. 2008).
In our experiment, oxygen production and dark respiration rates were negatively affected by temperature. Previous work suggested that respiration rates in M. vertebralis increases with increasing temperatures before and after exposure to 31 °C for several weeks (Uthicke et al. 2011). Despite the fact that an increase in temperature speeds up enzymatic reactions, explaining increased respiration rates in the short term, in the long term, a decline in respiration rates was observed. This shows that the holobiont was weakened in the 31 °C compared with the controls at the end of the experiment. Studies on corals also report reduced respiration rates with increasing temperature (Faxneld et al. 2011; Agostini et al. 2013).
We did not observe any effect of raised pCO2 alone on oxygen production and dark respiration. The result that dark respiration was not affected by pCO2 increase alone, is similar to studies in corals (Langdon et al. 2003; Reynaud et al. 2003). However, our results imply a significant synergistic interaction of the two stressors on the reduction of respiration rates in M. vertebralis. The synergistic inhibition of respiration observed in the combined treatment indicates that the metabolic rate of the holobiont is reduced, and this effect may propagate into other vital parameters.
Elevated pCO2 alone increased the amount of chl a in M. vertebralis but not in H. depressa. CO2 fertilisation is known to increase cell numbers, pigments, and productivity in marine unicellular plankton, for example cyanobacteria (Riebesell et al. 1993) and diatoms (Yang and Gao 2012). Productivity increase due to pCO2 increase has also been demonstrated in imperforate Foraminifera (Uthicke and Fabricius 2012) and cell counts of dinoflagellate symbionts in M. rossi showed higher symbiont density under elevated pCO2 (Reymond et al. 2013). It is therefore likely that the increased chl a content in M. vertebralis with pCO2 enhancement in our study reflects higher photosymbiont density. When Foraminifera were simultaneously exposed to elevated temperature, chlorophyll a content did decrease significantly, indicating that the hypothesised increase in photosymbiont density due to pCO2 fertilisation was counteracted by temperature, leading to trade-offs in the photosymbiont efficiency and density.
Survivorship and growth
Elevated temperature reduced survivorship in H. depressa but did not affect M. vertebralis, indicating that the latter species is more tolerant. Previous work on the temperature response of M. vertebralis also showed no effect on survivorship rate under exposure at 31 °C for several months, but reported reduced growth at this temperature (Uthicke et al. 2011). Elevated pCO2 did not influence survivorship in either species, which is similar to previous laboratory studies that reported no significant effect of pCO2 elevation on survivorship in several Foraminifera species (Vogel and Uthicke 2012; McIntyre-Wressnig et al. 2013). However, in H. depressa the combined effect of pCO2 and temperature on survivorship was significant and synergistic indicating that this species is especially vulnerable to the combination of stressors.
In our experiment, temperature and elevated pCO2 (738 µatm) in isolation reduced growth in the hyaline species H. depressa. In contrast, Vogel and Uthicke (2012) did not report negative effects on growth in H. depressa up to pCO2 levels of 1,600 µatm. The reason for these differences is not clear but we note that in our experiment the growth rate of H. depressa was higher by almost a factor of two than in the experiments by Vogel and Uthicke (2012). It is possible that more flow in our system caused higher growth rates in H. depressa, leading to significant differences between control and pCO2 treatments in this species (Table 2). Although we have measured growth as an increase in cell volume, it is likely that in both organisms, growth rate is linked with calcification. In this context, we note that flow rates as applied here may have led to a thinning of boundary layers on the surface of the Foraminifera, which may have influenced the scale of local changes of pH induced by photosynthesis and calcification (Glas et al. 2012). A positive influence of water motion on growth rate has been demonstrated in two earlier studies (ter Kuile and Erez 1984; Hallock et al. 1986). On the other hand, the response of growth and calcification in benthic Foraminifera may be decoupled with respect to the effect of pCO2 and the reaction might be species specific. For example, Amphistegina gibbosa did not exhibit negative effects on growth of up to 2,000 µatm pCO2, but showed patchy test dissolution (McIntyre-Wressnig et al. 2013). Elevated calcification rates were observed under intermediate pCO2 levels (580–770 µatm) for the clonal population of Baculogypsina sphaerulata, whereas the second hyaline species in the same study Calcarina gaudichaudii, showed an inconsistent reaction (Fujita et al. 2011). Furthermore, genotype-specific responses to ocean acidification have been reported for other marine organisms, such as coccolithophorids (Langer et al. 2009) and diatoms (Kremp et al. 2012).
In contrast, the porcelanous M. vertebralis showed no significant growth response to elevated temperature and pCO2 alone. For this species, growth rates in this study were in the same range as in the previous lower-flow setup (Uthicke et al. 2011; Vogel and Uthicke 2012). A small but not significant increase in growth was observed in M. vertebralis in the treatment exposed to elevated pCO2 (738 µatm) at 28 °C. A slight growth enhancement was observed in other porcelaneous species (Vogel and Uthicke 2012), whereas other studies reported reduced growth at medium to high pCO2 levels (700–1,100 µatm) in Amphisorus hemprichii (Fujita et al. 2011; Hikami et al. 2011) and M. rossii (Reymond et al. 2013).
Differences in the growth and calcification responses to pCO2 enhancement are known between and within taxonomic groups (Ries et al. 2009). Varying responses in calcification processes under intermediate scenarios of up to 900 µatm may reflect differential development of protective layers around the precipitated biomineral and different abilities to regulate the pH at the site of calcification (Ries et al. 2009). In our experiment, the moderately elevated pCO2 level acting alone may have released the photosymbiont population of M. vertebralis from CO2 limitation (Allemand et al. 2004), which would increase carbon translocation to the host and lead to a growth enhancement.
In all treatments in our study, the Ω Ca of the seawater remained above two (Table 1) and no test dissolution was observed in any of the treatments. Typically, test dissolution is observed in benthic Foraminifera exposed to much higher pCO2 conditions (2,000 µatm) and at much lower Ω Ar and Ω Ca of sea water than in our experiment (Haynert et al. 2011; McIntyre-Wressnig et al. 2013), although at natural CO2 vents, dissolution was observed already at pH ~7.9 (Uthicke et al. 2013). Test dissolution at pCO2 levels equivalent to a pH of 7.4–7.9 was also observed in M. vertebralis in laboratory culture (Sinutok et al. 2011), but specimens in the control treatment in that study also showed slight test dissolution; indicating that the cultured Foraminifera were not physiologically fit.
In summary, our results indicate that, at least in the short term, coral reef Foraminifera are likely to continue to grow under conditions predicted for the end of the century. However, the fact that in both studied species, growth was inhibited in the combined treatment indicates that in the long term, growth and by inference calcification under lower saturation may become more difficult. This may ultimately lead to ecological exclusion of these species as observed at present in CO2 seep systems (Dias et al. 2010; Uthicke and Fabricius 2012; Uthicke et al. 2013).
Combined effects of key global change stressors
Significant interactive effects between pCO2 and warming were observed for 50 % of the parameters investigated. In 75 % of these, for each species, the combined effects were synergistic—the effects of warming and elevated pCO2 led to a stronger physiological response than the sum of the effects of the individual parameters (Table 3). Because temperature and pCO2 may affect the holobiont as a whole, it is difficult to offer a physiological explanation for the prevalence of the synergistic effects. As a likely explanation, we suggest that the enhanced negative effects of multiple stressors could reflect trade-offs in resource allocation, where the costs of counteracting the effect of one stressor reduce the ability to counteract the effects of the additional stressor. Similarly, it has been suggested that under stressful environmental conditions, such as elevated inorganic nutrient levels, the pressure on the holobiont to control the population size of its photosymbionts might increase, reducing the capacity of the holobiont to respond to stress (Uthicke et al. 2011). The stress caused by over-growing population of photosymbionts has been described by Wooldridge (2009) to physiologically affect corals and lower their bleaching thresholds. Furthermore, a 3-yr field experiment demonstrated the same effect, where corals bleached more in artificial nutrient enrichment treatments (Vega Thurber et al. 2013).
Interactive negative effects between pCO2 and temperature have been shown to affect the calcification rate in corals, but the response of the corals was highly species specific (Edmunds et al. 2012). In an experiment increasing nutrient levels and elevating pCO2, photosymbiont concentration in M. rossi was reduced more under the combined stress than when individual stressors acted in isolation (Reymond et al. 2013). van Dam et al. (2012) showed that populations of Foraminifera exposed to the herbicide Diuron become disproportionately more sensitive to temperature and both factors acted additively on the foraminiferal photosynthetic response. Ecotoxicological studies on the interaction of climate change with additional stressors, such as pesticide exposure, indicate a prevalence of synergistic interactions across different organisms (Holmstrup et al. 2010; Kohler and Triebskorn 2013). In this respect, the observation on the numerous synergistic interactions in our study indicates that the physiology of the unicellular Foraminifera and/or their symbiosis with algae may be affected in a similar way as that of other organisms, contrary to the hypothesis by Pörtner (2002) that protists are less vulnerable to the studied stressors.
Irrespective of the exact mechanism responsible for the existence of strong synergistic effects between the key global change stressors tested in this study, our results indicate that the effects of environmental change in the shallow marine realm under expected CO2 emission scenarios are likely to be underestimated when the effects of elevated pCO2 and temperature are investigated in isolation.
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The study was funded by the Australian Institute of Marine Science and conducted with the support of funding from the Australian Government’s National Environmental Research Program. We are grateful for the assistance of M. Takahashi for developing the design and constructions of the flow-through housings. J. Brandt assisted with digital image analysis. The study benefited greatly for the help of F. Flores, S. Noonan, N. Webster, and A. Negri.
Communicated by Biology Editor Dr. Anastazia Banaszak
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Schmidt, C., Kucera, M. & Uthicke, S. Combined effects of warming and ocean acidification on coral reef Foraminifera Marginopora vertebralis and Heterostegina depressa . Coral Reefs 33, 805–818 (2014). https://doi.org/10.1007/s00338-014-1151-4
- Climate change
- Ocean acidification
- Benthic Foraminifera