Ocean warming and acidification act concurrently on marine ectotherms with the potential for detrimental, synergistic effects; yet, effects of these stressors remain understudied in large predatory fishes, including sharks. We tested for behavioural and physiological responses of blacktip reef shark (Carcharhinus melanopterus) neonates to climate change relevant changes in temperature (28 and 31 °C) and carbon dioxide partial pressures (pCO2; 650 and 1050 µatm) using a fully factorial design. Behavioural assays (lateralisation, activity level) were conducted upon 7–13 days of acclimation, and physiological assays (hypoxia tolerance, oxygen uptake rates, acid–base and haematological status) were conducted upon 14–17 days of acclimation. Haematocrit was higher in sharks acclimated to 31 °C than to 28 °C. Significant treatment effects were also detected for blood lactate and minimum oxygen uptake rate; although, these observations were not supported by adequate statistical power. Inter-individual variability was considerable for all measured traits, except for haematocrit. Moving forward, studies on similarly ‘hard-to-study’ species may account for large inter-individual variability by increasing replication, testing larger, yet ecologically relevant, differences in temperature and pCO2, and reducing measurement error. Robust experimental studies on elasmobranchs are critical to meaningfully assess the threat of global change stressors in these data-deficient species.
Climate change threatens marine ectotherms via myriad global change phenomena1. Owing to anthropogenic carbon emissions, the oceans are experiencing changes in physicochemical properties at an unprecedented rate. Unabated climate change projections for the year 2100 suggest that sea surface temperatures will increase by 3–5 °C (ocean warming), and carbon dioxide partial pressures (pCO2) will increase by ~ 600 µatm (ocean acidification; OA) in pelagic environments; projections are more extreme and variable in coastal environments2. These global change phenomena are predicted to affect the fitness and survival of marine ectotherms through reductions in an organism’s physiological oxygen supply capacity3. However, alternative hypotheses argue for characterising physiological performance across multiple levels of biological organisation4.
Multiple physiological systems are predicted to be affected by global change stressors, including those associated with behaviours. Changes in behaviour in temperate and tropical marine ectotherms are generally associated with simulated OA5 conditions in a laboratory setting, such as changes in the strength and direction of lateralisation6, predator avoidance7, and activity levels8. Beyond behavioural performance, well-documented physiological effects of simulated OA conditions include respiratory acidosis (e.g., via reduced extracellular pH) and altered acid–base homeostasis (e.g., via bicarbonate buffering), production of lactate (e.g., via reliance on anaerobic metabolism), and reduced survival9. The physiological and behavioural responses to simulated ocean warming conditions have also been well-studied under laboratory conditions; indeed, several thermal tolerance mechanisms are under consideration3,4.
Ocean warming and acidification can affect the physiology of marine ectotherms interactively. There is inherent value in quantifying the effects of isolated stressors, but marine environments will be exposed to multiple global change stressors10. Interactive effects can be synergistic (i.e., both stressors disproportionately influence effect size), additive (i.e., both stressors contribute individually to effect size), or antagonistic (i.e., exposure to one stressor negates or ‘masks’ the effect of another)11. A recent meta-analysis demonstrated that ocean warming and acidification act additively on aerobic scope (i.e., the difference between maximum and standard metabolic rate) in marine ectotherms; yet, mechanisms underlying interactive effects of ocean warming and acidification are unknown1. Deleterious, negative interaction effects are, therefore, unpredictable. Despite the complexity of responses observed to date for an impressive diversity of marine taxa, ecological roles, and habitat types, pervasive knowledge gaps remain.
Global change effects on the physiology of large predatory fishes represent a general knowledge gap12. As mesopredators and apex predators, these species can exert top-down control in ecosystems13. Work with larger specimens is restricted by equipment used to measure physiological performance traits, such as swim flumes and respirometry chambers, and the ability to treat enough replicate individuals; however, studying early life stages can be amenable to available equipment and holding in captivity to ensure that enough replicate individuals are treated. Evidence suggests that early-life stages of teleost fishes (e.g., embryos and larvae) are more sensitive to elevated pCO2 and temperatures than their adult counterparts14,15, thus emphasizing the importance of studying this life-stage to understand a populations’ or species’ vulnerability. Early-life stages of elasmobranch fishes (e.g., sharks) are fully developed at birth/hatch and, therefore, differ considerably from teleost fishes that undergo metamorphosis; yet, the biological ramifications of multiple global change stressors have not been investigated for large predatory elasmobranch fishes at any life stage16.
Some shark species rely on shallow, nearshore habitats as nursery areas during early life. These habitats are thought to improve fitness relative to individuals or populations that do not use nursery areas17. Neonates can exhibit strong site fidelity to nursery areas17, such that these habitats can become ecological traps during extreme conditions such as heatwaves18. Indeed, recent studies on volitional activity found that juvenile sharks and rays within nursery areas routinely live at or above temperatures that reduce activity19. However, shark species that use such habitats during early ontogeny (e.g., shark/egg nursery areas) have demonstrated resilience to OA-relevant conditions and capacity for reversible acclimation to ocean warming conditions16. Conversely, some elasmobranch fishes exhibit unpredictable, deleterious responses to interacting global change stressors20. Shark species that derive fitness benefits from shark nursery areas could therefore be at risk if these habitats transition under climate change from nursery areas to ecological traps.
We designed a study with the intention of evaluating responses of reef shark neonates to global change stressors. The first study objective was to identify ex situ physiological and behavioural responses of blacktip reef shark (Carcharhinus melanopterus) neonates upon short-term acclimation to various temperature and pCO2 conditions. To do this, we employed a simple, yet fully factorial, experimental design including two temperature and two pCO2 levels and three replicate groups of 3–4 sharks (i.e., 9–10 sharks) per treatment. Ecologically relevant temperatures (28 and 31 °C) were selected because they represent average dry and wet season temperatures, respectively21. Further, pCO2 values (650 and 1050 μatm) were selected because they represent a high pCO2 value that blacktip reef shark neonates currently experience in situ and a mild (+ 400 μatm) acidification scenario22, respectively. Brief (i.e., two-week) exposure to static environmental conditions was intended to provide a basic understanding of responses to multiple environmental stressors. Upon exposure, we assessed behavioural (lateralisation and activity) and physiological (hypoxia tolerance, oxygen uptake rates, and acid–base and haematological status) metrics that would encompass the broad range of possible responses observed for elasmobranch fishes and those that had been previously documented in the literature16. Because sharks are among the classically ‘hard-to-study’ species in experimental biology, the second and third study objectives were, respectively, to investigate the power of our study design and to quantify the degree of inter-individual variability so that we may make recommendations for future research on similarly difficult species. Robust experimental studies of global change stressors are in need for species like sharks, where slow life-history traits may disproportionately put them at risk of population declines and extirpation in response to global change stressors16.
Behavioural metrics were quantified after 7–13 days of exposure to treatment conditions (Table 1). Behavioural lateralisation was quantified after seven days of exposure using a two-way T-maze in untreated water7. We were unable to detect treatment effects on the relative lateralisation index (LR; turning preference scored from − 100 to 100, where positive LR indicates a right turning bias; Fig. 1A). Further, the distribution of LR (Kolmogorov–Smirnov test, D = 0.256–0.556, p > 0.100) and variance of LR (Bartlett test, K2 = 3.86, p = 0.276) did not differ between treatment groups. We also did not detect treatment effects on the absolute lateralisation index (LA; strength of lateralisation from 0–100; Fig. 1B) or differences between treatment groups for the variance of LA (Bartlett test, K2 = 5.31, p = 0.150).
Volitional activity levels were quantified after 8–13 days of exposure to treatment conditions using accelerometers. To do this, one shark was tagged at a time with an externally attached accelerometer and was then isolated in a 1250 L (1.5 m diameter and 70 cm deep) tank under treatment conditions. After allowing for a two-hour recovery period from the tagging procedure, mean activity levels were calculated over a four-hour window (i.e., 1100–1500) on the day of testing for each shark. We did not detect treatment effects on activity levels, as defined by overall dynamic body acceleration (ODBA, in g; Fig. 1C).
Physiological metrics were quantified after 14–17 days of exposure to treatment conditions in the same sharks that underwent behavioural assays (Table 2). Hypoxia tolerance was quantified after 14 days of exposure (Fig. 2). To do this, the oxygen level of an experimental tank containing a single shark was lowered at a constant rate with nitrogen gas. An individual shark’s hypoxia tolerance was recorded as the oxygen level (as a percent of air saturation) at which the shark first exhibited muscle spasms; there were no detectable effects of treatment conditions.
Oxygen uptake rates (ṀO2, in mg O2 kg−0.89 h−1) were quantified using intermittent-flow respirometry and mass-corrected using an intraspecific scaling exponent of 0.8923 (Fig. 3). Our models did not detect significant effects of treatment conditions on minimum oxygen uptake rates (ṀO2Min), maximum oxygen uptake rates (ṀO2Max), absolute aerobic scope (AAS = ṀO2Max-ṀO2Min), factorial aerobic scope (FAS = ṀO2Max·ṀO2Min−1), excess post-exercise oxygen consumption (EPOC; the oxygen consumed during recovery, in mg O2 kg-0.89), or recovery time.
Acid–base and haematological metrics were quantified from blood samples drawn after sharks had been exposed to treatment conditions for 17 days (Fig. 4). An effect of pCO2 was detected on whole blood lactate concentration (in mmol L−1), where lactate concentration was lower at higher pCO2 levels. Our models also detected a significant effect of temperature on haematocrit (Hct; the ratio of erythrocyte volume to whole blood volume), where Hct was higher at 31 °C relative to 28 °C. Conversely, no treatment effects were detected for blood pH, haemoglobin concentration ([Hb], in mmol L−1), or mean corpuscular haemoglobin concentration (MCHC, in mmol L−1).
A synergistic effect between temperature and pCO2 was initially detected for ṀO2Min (observed power = 54%); yet, there was not enough power (i.e., > 80%) to conclude whether there were – or were not – interaction effects. Removing the temperature × pCO2 interaction term from our models still did not sufficiently increase the power of our models (observed power = 62%). As such, we are unable to claim whether pCO2 affected lactate. However, there was sufficient power (i.e., 98%) to test for effects of temperature on Hct, and thus we are confident that the observed effect was genuine.
To make recommendations for future study designs, we employed a Monte Carlo simulation based power analysis approach24 to estimate the sample size (i.e., replicate groups) required to observe significant treatment effects under our temperature and pCO2 conditions. We did not consider increasing the number of samples within replicate groups owing to logistical constraints (e.g., number of sharks that could be maintained per tank). First, we identified the number of replicate groups needed to yield enough power to significantly detect our observed treatment effect sizes using ṀO2Min, which is a representative and well-studied metric across climate change studies in marine ectotherms1. At least eight replicate groups (n = 96 sharks) per treatment would be needed to detect the effects of elevated pCO2 (ΔṀO2Min = 22.3 mg O2 kg−0.89 h−1) and at least five replicate groups (n = 60 sharks) per treatment would be needed to detect the interaction between temperature and pCO2 (ΔṀO2Min = 46.6 mg O2 kg−0.89 h−1). The observed temperature effect was half that of the predicted pCO2 effect size and small enough such that increases in the number of replicate groups did little to ameliorate power issues.
Finally, using predicted ṀO2Min values measured for various marine ectotherm taxa (i.e., including teleost and elasmobranch fishes) from a recent meta-analysis1, temperature, pCO2, and interaction effect sizes were manipulated in our ṀO2Min model to demonstrate an ‘a priori’ experimental design approach. From this, we determined that our original experimental design of including three replicate groups per treatment had sufficient power to detect the predicted interaction effect and the predicted temperature effect. The predicted pCO2 effect on ṀO2Min was similarly negligible to the observed temperature effect of the original model.
Of the all measured physiological traits, lactate concentration, [Hb], MCHC, EPOC, and recovery time exhibited considerable within-group variation (coefficient of variation, CV > 30%). Haematocrit exhibited the lowest within-group variation of any measured trait (CV = 8.4%). After controlling for mass, ṀO2Min, ṀO2Max, and FAS had CVs of 15.3, 17.7, and 18.8%, respectively. Absolute aerobic scope was considerably more variable, with a CV of 27.2%. For behavioural traits, LA exhibited tremendous within-group variability (CV = 44.9%). Although ODBA was less variable (CV = 12.3%), this trait exhibited 1.2–1.6-fold variation across treatment groups. Excluding comparisons that were associated through calculations (i.e., MCHC and [Hb], EPOC and recovery, aerobic scope and ṀO2Min and ṀO2Max), there were no strong correlations (i.e., Pearson’s r > 0.80, p < 0.001) within or between any measured physiological or behavioural traits.
The purpose of this study was to gain insight into the responses of blacktip reef shark neonates upon exposure to elevated temperatures and pCO2 levels resembling end-of-century climate change conditions and comment on experimental design and sources of variability. Blacktip reef shark neonates exhibited an increase in Hct upon exposure to 31 °C when compared to sharks maintained at 28 °C. Other statistically significant effects (i.e., lower blood lactate concentrations in sharks maintained at 1050 μatm pCO2 and a synergistic temperature and pCO2 effect on ṀO2Min) were not supported by enough power to claim that these were genuine effects of treatment. Our analyses revealed, however, that our study design was sufficient to meaningfully detect the presence or absence of treatment effects, at least on ṀO2Min, for which there are sufficient data to inform such analyses1. Instead, due to the variability present in our data, we would need to double the number of replicate groups in our experimental design to be confident that our results (i.e., effects and null effects) were statistically robust. Indeed, this variability likely stems from biological (i.e., inter-individual variability) and experimental sources. We further discuss the potential significance of our findings and highlight logistical considerations for future studies investigating global change stressors in data-deficient and hard-to-study species, such as medium-to-large-bodied sharks.
Temperature acclimation affected the haematological status of blacktip reef sharks. Sharks acclimated to 31 °C for two weeks had a higher Hct than sharks maintained at 28 °C. In teleost fishes, Hct is elevated through a combination of red blood cell swelling, the release of additional erythrocytes into circulation (e.g., from the spleen), and movement of fluid from plasma to interstitial spaces25. In blacktip reef shark neonates from the same population examined in this study, Hct increased in response to exercise stress; although, the mechanism underpinning this increase is not yet known26. However, Hct did not vary over a 28–31 °C diel temperature range in wild-caught blacktip reef shark neonates from the same population examined in this study27. The observed elevation in Hct could compensate for decreases in the affinity of Hb for oxygen that has been documented in vitro with acute warming21. Additionally, the increase in Hct at 31 °C may be associated with increases in hypoxia tolerance and thermal tolerance, which has been previously documented for blacktip reef sharks upon four weeks acclimation to 31°C21. Previous research in notothenioid fishes and Chinook salmon (Oncorhynchus tshawytscha) suggests that Hct is positively associated with critical thermal maximum, a thermal tolerance metric28,29. Further, as thermal tolerance and hypoxia tolerance are associated in blacktip reef sharks, an increase in Hct may further support the hypothesis of a common acclimation response and oxygen-dependent mechanism underlying these traits3. From an ecological perspective, the consequences of elevated Hct in blacktip reef shark neonates would be experienced in situ during marine heatwaves, such as those that have been occurring with increasing frequency at a similar latitude on the Great Barrier Reef30. Elevations in Hct at such high temperatures may lead to exponential increases in blood viscosity that could ultimately affect oxygen transport31. Therefore, further investigation into the ecological consequences of haematological responses to warming in reef shark neonates are warranted.
Significant effects of temperature and pCO2 were detected for several physiological traits. A negative effect of elevated pCO2 was detected for blood lactate concentration, and a synergistic effect of temperature and pCO2 was detected for ṀO2Min. However, inter-individual variability in lactate (CV = 45.8%) and ṀO2Min (CV = 15.3%) was considerable, and the observed power was too low (i.e., < 80%) for us to be confident in these responses. Indeed, acute (i.e., 72-h) exposure to elevated pCO2 had the opposite effect on blood lactate concentration in blacktip reef shark neonates22. At least for ṀO2Min, robust statistical power could have been achieved with additional replicate groups, provided that inter-individual variability did not increase. As variability in mass-corrected ṀO2Min of blacktip reef shark neonates was within the range reported in teleost fishes32, it does not seem likely that additional sampling of similarly sized individuals would increase variability. A few other studies have documented synergistic effects of warming and acidification on ṀO2Min in teleost fishes; yet, temperature and pCO2 are predicted to interact antagonistically on ṀO2Min across a wide array of marine ectotherm taxa1. If temperature and pCO2 truly act synergistically on ṀO2Min in blacktip reef sharks, this could reflect the increased costs of maintaining acid–base homeostasis in the altered environment. Within an ecological context, environmental oxygen partial pressures (pO2) in blacktip reef shark neonate habitats around Moorea are routinely supersaturated such that elevations in ṀO2Min would not be problematic in the context of oxygen availability. Conversely, increased maintenance metabolism costs would necessitate increased foraging success, which is already quite low in the study population33 and an increased demand could lead to starvation34. Interestingly, supposed changes in ṀO2Min were not reflected in absolute or factorial aerobic scope, possibly owing to variability in ṀO2Min and ṀO2Max and because FAS and AAS estimates were low relative to other fishes35. Whilst a lack of correlation between ṀO2Min and ṀO2Max across individuals is possible36, its absence suggests the possibility of measurement error, likely in ṀO2Max for which best practice has not been established in sharks37. Therefore, additional research is required to confidently detect effects of temperature (alone and interacting with elevated pCO21) on ṀO2Min in blacktip reef sharks.
A simple, fully factorial experimental design with two temperature and pCO2 levels was statistically robust. However, of the 15 metrics and 45 possible treatment effects, only three statistically significant effects were detected with only one supported by adequate statistical power. Minimum ṀO2 is a commonly measured trait in laboratory studies assessing climate change effects in marine ectotherms1. In the present study, sufficient power to confidently detect observed temperature, pCO2, and interaction effects on ṀO2Min could be achieved with additional replicates; although, a priori power analyses based on a comprehensive meta-analysis across marine ectotherm taxa suggested that our simple experimental design was sufficient1. Power analyses for future studies of climate change effects in sharks and rays are limited by very few studies having tested sharks and rays under both temperature and pCO2 conditions16. The issues with statistical power in the present study also inform interpretation of null effects. In other words, does the absence of a significant result imply no effect of treatment, given the observed variability in measured behavioural and physiological traits? A frequentist interpretation (i.e., p-value hypothesis testing) of a failure to reject a null hypothesis cannot support this claim; whereas, the approach employed in the present study (i.e., confidence intervals of effect size) can explain whether an effect size overlaps with zero or some practically marginal value38. For instance, blacktip reef shark neonates exposed to elevated temperature and pCO2 conditions were predicted to, on average, exhibit ṀO2Min values that were 46.6 mg O2 kg−0.89 h−1 higher than sharks exposed to ambient temperature and pCO2 conditions, but this difference could have been as great as 91.8 mg O2 kg−0.89 h−1 or as little as 0.4 mg O2 kg−0.89 h−1. Practically, this demonstrates that some sharks responded strongly to treatment (i.e., a 62% increase in ṀO2Min); whereas, others did not respond at all. Certainly, the influence of inter-individual variability in traits can be confounding and draw scepticism toward effects and null effects39. Identifying and controlling those sources of variability is a critically important endeavour to ensure accurate and reliable estimations of simulated climate change stressor effects in such data deficient groups as sharks and rays.
Blacktip reef shark neonates exhibited inter-individual variation in physiological traits that was not consistent across individuals. Variation in most traits was considerable (i.e., CV > 12%, except for Hct), but within ranges reported for both teleost and elasmobranch fishes. However, interpretation of variability in traits is difficult. Lateralisation exhibits high and context-dependent variability40 but has not been widely studied in sharks41. Alternatively, for a trait like ODBA for which sources of measurement error in sharks are understood, observed variability is likely due to accelerometers being too large42, dorsal fins of neonates not being rigid enough for attachment43, and the brevity of monitoring that precluded us from accounting for circadian activity rhythms. Among haematological traits, variability in blood pH, for instance, can result because arterial blood cannot be selectively sampled in elasmobranch fishes using caudal puncture44. Variation in ṀO2Min and ṀO2Max fell within ranges reported in teleost fishes, whilst variation in aerobic scope was greater32. Intrinsic sources of intra-specific variability in metabolic rates (i.e., ṀO2Min, ṀO2Max, AAS) are thought to include genetic, developmental, and biochemical sources of origin, among others45. Indeed, genetic variation may account for some variability in these traits; although, blacktip reef sharks around Moorea exhibit inbreeding and low genetic diversity46. Extrinsic sources (e.g., local abiotic conditions, food availability) could be at play, given that sub-populations of blacktip reef shark neonates around Moorea occupy such small home ranges47 and exhibit variable foraging success33. Conversely, the small spatial scale and somewhat homogenous coastline of Moorea48 could mean that blacktip reef shark neonate habitats do not differ greatly in abiotic conditions. Further, there were no correlations between physiological and behavioural traits8. A lack of consistent associations between traits across individuals meant that sharks could not be coded as ‘high responders’ and ‘low responders’ as a way to control for inter-individual variability39. As such, it is difficult to discern whether variation in traits is biologically meaningful, such that climate change ‘winner’ and ‘loser’ phenotypes can be identified.
In conclusion, our findings provide a stepping stone forward but also show the need for more robust and extensive studies to definitively identify the effects of elevated temperature and pCO2 conditions in a large predatory elasmobranch fish. Indeed, the present study recommends at least a doubling of replicate groups that should be tested in a simple 2 × 2 experimental design, which, in this case, would involve collecting and testing half of the annual neonate population around Moorea, which is not practically feasible. Moving forward, reducing measurement error for traits like activity level and metabolic rate will be paramount in future studies on active shark species and will possibly involve the development and validation of custom equipment, including respirometry systems49,50 and data-loggers42,51. Controlling for inter-individual variation is likely to be the more challenging endeavour, but this could be addressed by increasing the difference in temperature and pCO2 conditions between treatments. Statistical approaches that move beyond frequentist null hypothesis testing may also shed light on the interpretation of null results38. However, low pCO2 is difficult to achieve, even at low stocking densities with large fish in field locations22,52, and much higher pCO2 conditions are not relevant to end-of-century climate change projections. Acclimation to higher test temperatures than used in this study can result in mortality21, which is an unacceptable endpoint for a protected species like the blacktip reef shark. Indeed, experimentally testing temperature effects on the physiological performance of large-bodied, active sharks has only been accomplished for several species19,34,51,53, and testing the effects of elevated pCO2 has only been accomplished in one study22. Therefore, research is critical to provide unequivocal, empirical evidence that yields consensus toward a physiologically-informed framework to inform responsible management for these classically ‘hard-to-study’ species that are already – or will be – threatened by global change.
All methods were carried out in accordance with relevant guidelines and regulations. Permission to collect, possess, and transport sharks and shark tissues was obtained from the French Polynesian Ministère de la Promotion des Langues, de la Culture, de la Communication, et de l’Environnement (Arrêté N°5129). Ethical approval for all experiments described herein was obtained from the James Cook University (JCU) Animal Ethics Committee (protocol A2394).
Neonatal blacktip reef sharks (n = 37, total length = 569.2 ± 31.9 mm, mass = 1.0 ± 0.2 kg; data presented are means ± standard deviation unless noted otherwise) were collected from putative shark nursery areas around the island of Moorea, French Polynesia from October 2018 through January 2019. Sharks were fished at dusk using monofilament gill-nets (50 m by 1.5 m, 5 cm mesh size), and were transported in 200 L coolers of aerated seawater to a laboratory facility. We marked sharks for identification with uniquely coloured spaghetti tags (Hallprint, Hindmarsh Valley, SA, Australia) and passive integrated transponders (Biolog-id SAS, Paris, France). Animals were held under natural photoperiod in flow-through, 1250 L circular tanks (3–4 sharks per tank) and were fed ad libitum every second day with fresh tuna (Thunnus spp.) except for 24–48 h of fasting prior to testing. Feeding was monitored to ensure that all sharks ate during each feeding event. On average, sharks gained mass and did not change in body condition while in captivity. Following experimentation, after 21–34 days in captivity, sharks were released in good condition at their original capture site.
Sharks were acclimated to combinations of temperature (28 and 31 °C) and pCO2 (650 and 1050 µatm) that are representative of ambient conditions of Moorea’s lagoon and projected end-of-century pCO2 in a fully factorial design (Table 3). Acclimation to temperatures above 31 °C is associated with mortality, and thus temperatures higher than 31 °C were avoided21. Three replicate groups of 3–4 sharks were tested at each temperature and pCO2 combination, and up to four replicate tanks could be tested at any given time. Experiments were conducted between November 2018 and January 2019, and replicates within treatments were conducted across the entire study period. Behavioural assays were conducted at seven days (lateralisation) and 8–13 days (activity levels) of acclimation, as behavioural responses are apparent after several days at high pCO25,16. Physiological assays were conducted after 14 days (hypoxia tolerance), 16 days (oxygen uptake rates), and 17 days (acid–base and haematological status) of acclimation.
After habituation, temperature conditions were achieved in 0.5 C d−1 increments using aquarium heaters (Jager 300w, EHEIM GmbH & Co KG, Deizisau, Germany) or chillers (TK-1000/2000, TECO S.r.l., Ravenna, Italy)21. Elevated pCO2 conditions were achieved once target temperatures were reached. Unique header tanks (288 L) for each pCO2 treatment tank were dosed with CO2 using a pH controller system (AT Control System, AB Aqua Medic GmbH, Bissendorf, Germany) set to pH values on the National Bureau of Standards scale (pHNBS).
Four physicochemical parameters were measured to calculate seawater pCO2: pHNBS, total alkalinity, temperature, and salinity55. Holding tank pHNBS was measured daily with a handheld meter (Seven2Go Pro, Mettler-Toledo GmbH, Greifensee, Switzerland) and was calibrated as needed with pHNBS 4 and 7 buffer solutions. Data-loggers (DS1922L, Maxim Integrated Products, Inc., San Jose, CA, USA) recorded temperatures hourly. Salinity was measured daily with a handheld refractometer. Total alkalinity (AT, µmol kg seawater−1) of holding tank water was measured via open-cell Gran titration following standard operating procedure 3b56. Seawater samples (50 mL) were dosed with 0.1 M HCl in 0.1 mL increments, and AT was calculated using custom R script (F. Gazeau, unpublished data). The titrator system (Metrohm 888 Titrando, Metrohm AG, Herisau, Switzerland) was calibrated against certified reference materials (Professor A.G. Dickson, Scripps Institution of Oceanography, San Diego, CA, USA, batch number 171). Water samples were collected three times for each replicate tank: once target temperature and pHNBS conditions were achieved, and after one and two weeks of acclimation. Finally, pCO2 was calculated by inputting pHNBS, temperature, salinity, and AT into CO2SYS54 alongside K1 and K2 constants by Mehrback and colleagues refit by Dickson and Millero57,58 and KHSO4 by Dickson.
Lateralisation was tested using a detour test in a two-way T-maze (69 cm long by 21 cm wide). Sharks were tested under ambient conditions because behavioural responses to high pCO2 persist during acute exposure to ambient conditions7. After a five-minute habituation, turning direction was scored as sharks exited the maze. Ten turns were recorded at either side of the maze – to account for potential asymmetry of the maze – totalling 20 turning decisions per shark. The relative lateralisation index (LR; turning preference scored from − 100 to 100, where positive LR indicates a right turning bias) and absolute lateralisation index (LA; strength of lateralisation from 0–100) were calculated as LR = [(right turns – left turns)/sum of turns]·100, and LA =|LR|6.
Volitional activity levels were quantified using accelerometers (G6A + , Cefas Technology Limited, Suffolk, UK). Accelerometers were uniformly mounted on the right side of the first dorsal fin as described in Bouyoucos et al.21. Sharks were tagged by 0900 each day of testing and were then isolated in individual holding tanks under treatment conditions. Prior to deployment, accelerometers were rotated through each axis for calibration43. Tags recorded acceleration at 25 Hz, and dynamic acceleration was separated from raw acceleration data using a two-second running mean in Igor Pro (WaveMetrics Inc., Lake Oswego, OR, USA)51. Overall dynamic body acceleration (ODBA) was calculated as the sum of absolute values of dynamic acceleration in each axis43. Activity level was quantified as the mean ODBA recorded from 1100–1500, which is enough time (i.e., two hours) for juvenile sharks to resume consistent activity after capture, handling, and tagging59. Accelerometers weighed 5.2 g in water (i.e., a 9–18% increase in sharks’ apparent submerged weight) and had a frontal area of 476 mm2 (i.e., a 10–19% increase in sharks’ frontal area). Tag burden should be assessed in future studies, as it has implications for the accuracy of ODBA data42.
To quantify hypoxia tolerance, sharks were tested individually in a circular pool (100 L, 1 m diameter) under treatment conditions. After five minutes of habituation, oxygen saturation was lowered (8.9 ± 2.4% air saturation min−1) by bubbling nitrogen gas into the water. Oxygen saturation was monitored continuously with a Firesting Optical Oxygen Meter (PyroScience GmbH, Aachen, Germany). The onset of muscle spasms (OS) was used as a non-lethal experimental endpoint21; the oxygen saturation at OS was recorded to quantify hypoxia tolerance. Sharks were immediately returned to their treatment tank at the conclusion of the test.
Oxygen uptake rates (ṀO2, mg O2 kg−0.89 h−1) were quantified using intermittent-flow respirometry60. Sharks underwent a single respirometry trial to measure their minimum ṀO2 (ṀO2Min) and maximum ṀO2 (ṀO2Max). To accomplish this, sharks were first exercised (three minutes of chasing and one minute of air exposure) in a pool (100 L, 1 m diameter) under treatment conditions to achieve ṀO2Max immediately post-exercise60. Sharks were then transferred to the same respirometry system described by Bouyoucos et al.27 for 24 h of ṀO2 determinations (n = 96) to achieve ṀO2Min61. Following respirometry, sharks were weighed and returned to their treatment tank. Background ṀO2 (ṀO2Background) was measured in empty chambers immediately before and after respirometry with sharks.
Briefly, ṀO2 was calculated as the absolute value of the slope of the linear decline in dissolved oxygen (mg O2 L−1 s−1, extracted using custom R code; A. Merciere & T. Norin, unpublished data) with a coefficient of determination greater than 0.95 during each determination and corrected by the volume of water in respirometry chambers. Because of variation in shark mass (range = 0.7–1.4 kg), ṀO2 was allometrically scaled to 1 kg using a mass-scaling coefficient of 0.8923. Shark ṀO2 was corrected for background respiration by fitting a line to the two ṀO2Background measurements and subtracting the interpolated value from each ṀO2 determination60. Six ṀO2 metrics were then calculated. First, ṀO2Min (1) was calculated with the Mean of the Lowest Normal Distribution method outlined by Chabot et al.61. Next, ṀO2Max (2) was calculated from the highest slope measured over consecutive 30 s intervals during the first hour of respirometry27. Both absolute aerobic scope (AAS = ṀO2Max–ṀO2Min; 3) and factorial aerobic scope (FAS = ṀO2Max·ṀO2Min−1; 4) were calculated. Excess post-exercise oxygen consumption (EPOC, mg O2 kg-0.89; 5) was calculated as the area bound by an exponential decay curve fit to ṀO2, ṀO2Min, and the intersection of these curves27; this intersection was recorded as sharks’ recovery time (6) following exercise.
Blood samples (1 mL) were collected immediately after removing sharks from respirometry27. Samples were collected using caudal puncture with 23-gauge, heparinised needles. Whole blood pH (1) was measured with a temperature-correcting pH meter (HI98165, Hanna Instruments, Victoria, Australia) and correction equations for subtropical sharks62. Whole blood lactate concentration (mmol L−1; 2) was measured with an Accutrend Plus (Roche Diagnostics Ltd., Rotkreuz, Switzerland)27. Blood samples were centrifuged (10,000 g for three minutes) in duplicate to measure haematocrit (Hct, %; 3). Haemoglobin (Hb) concentration ([Hb], mmol L−1; 4) was measured by incubating 5 µl of whole blood in 1 mL of Drabkin’s reagent (potassium cyanide – potassium ferricyanide; Sigma-Aldrich, St. Louis, MO, USA) for at least 15 min and measuring absorbance of 200 µl aliquots in triplicate in a 96 well plate. Absorbance was read at 540 nm and [Hb] was calculated with an extinction coefficient of 11 mmo L−1 cm−163. Finally, mean corpuscular haemoglobin concentration (MCHC, mmol L−1; 5) was calculated as [Hb]·Hct−1.
Behavioural and physiological assays yielded 15 metrics: LR, LA, ODBA, hypoxia tolerance, ṀO2Min, ṀO2Max, AAS, FAS, EPOC, recovery time, whole blood pH, whole blood lactate concentration, Hct, [Hb], and MCHC. All metrics were fit with linear mixed effects models assuming Gaussian distributions using the R package ‘lme4′64,65, with temperature and pCO2 as interacting nominal fixed effects and replicate group as a random effect. Whilst model assumptions were met, linear mixed effects models are generally robust to violations of distributional assumptions66. Models including interaction terms were compared against nested models without interaction terms to estimate power to detect interactions using the ‘simr’ R package24. Models with interaction terms were only tested if power was > 80%. Then, the observed power of significant treatment effects could be estimated for the resulting models. Significance of fixed effects was determined by generating 95% confidence intervals (CI) of fixed effect estimate distributions from 1000 posterior simulations that were run using the R package ‘arm’67.
An additional series of analyses were conducted for lateralisation metrics. Frequency distributions of LR were compared between treatments with Kolmogorov–Smirnov tests6. Variances of LR and LA were compared between treatments with Bartlett tests of homogeneity of variances6.
Power analysis was used to estimate the number of replicate groups needed to confidently test for effects of temperature, pCO2, and their interaction on ṀO2Min using a simple 2 × 2, fully factorial design. For this analysis, we used our model for ṀO2Min of blacktip reef shark neonates from the first objective. The number of replicate groups in each model was increased using the ‘simr’ R package until increases in power plateaued above 80%. Then, we specified expected temperature, pCO2, and interaction effect sizes in our models using generic estimates from Lefevre’s meta-analysis of climate change effects on ṀO2Min in marine ectotherms1. A mean effect size for each variable was calculated using available data from all marine taxa in the meta-analysis, which included teleost (n = 13 species) and elasmobranch (n = 1) fishes. Calculated effect sizes (i.e., ratios of measured values for treatment vs control) were 1.67 for temperature, 1.06 for pCO2, and 1.60 for their interaction.
Coefficients of variation (CV, %) were calculated for each metric to quantify inter-individual variability. Then, associations between all traits were tested for using Pearson’s correlation tests. Statistically significant correlations were determined with a Bonferroni-corrected α = 0.0005 to account for multiple comparisons (n = 105).
Data presented in this manuscript are available from the Research Data Repository (Tropical Data Hub) at JCU: https://dx.doi.org/10.25903/5da407f2406f5.
Lefevre, S. Are global warming and ocean acidification conspiring against marine ectotherms? A meta-analysis of the respiratory effects of elevated temperature, high CO2 and their interaction. Conserv. Physiol. 4, cow009 (2016).
Field, C. B. et al. Technical Summary. Climate Change 2014: Impacts , Adaptation, and Vulnerability. Part A: Global and Sectoral Aspects. Contribution of the Working Group II to the Fifth assessment Report of the Intergovernmental Panel on Climate Change (2014).
Pörtner, H.-O., Bock, C. & Mark, F. C. Oxygen- and capacity-limited thermal tolerance: Bridging ecology and physiology. J. Exp. Biol. 220, 2685–2696 (2017).
Clark, T. D., Sandblom, E. & Jutfelt, F. Aerobic scope measurements of fishes in an era of climate change: Respirometry, relevance and recommendations. J. Exp. Biol. 216, 2771–2782 (2013).
Tresguerres, M. & Hamilton, T. J. Acid–base physiology, neurobiology and behaviour in relation to CO2-induced ocean acidification. J. Exp. Biol. 220, 2136–2148 (2017).
Domenici, P., Allan, B., McCormick, M. I. & Munday, P. L. Elevated carbon dioxide affects behavioural lateralization in a coral reef fish. Biol. Lett. 8, 78–81 (2012).
Munday, P. L. et al. Effects of elevated CO2 on predator avoidance behaviour by reef fishes is not altered by experimental test water. PeerJ 4, e2501 (2016).
Laubenstein, T. et al. Correlated effects of ocean acidification and warming on behavioral and metabolic traits of a large pelagic fish. Diversity 10, 35 (2018).
Heuer, R. M. & Grosell, M. Physiological impacts of elevated carbon dioxide and ocean acidification on fish. AJP Regul. Integr. Comp. Physiol. 307, R1061–R1084 (2014).
Boyd, P. W. et al. Experimental strategies to assess the biological ramifications of multiple drivers of global ocean change-A review. Glob. Chang. Biol. 24, 2239–2261 (2018).
Harvey, B. P., Gwynn-Jones, D. & Moore, P. J. Meta-analysis reveals complex marine biological responses to the interactive effects of ocean acidification and warming. Ecol. Evol. 3, 1016–1030 (2013).
Nagelkerken, I. & Munday, P. L. Animal behaviour shapes the ecological effects of ocean acidification and warming: Moving from individual to community-level responses. Glob. Chang. Biol. 22, 974–989 (2016).
Hammerschlag, N. et al. Ecosystem function and services of aquatic predators in the anthropocene. Trends Ecol. Evol. 34, 369–383 (2019).
Pörtner, H.-O. & Peck, M. A. Climate change effects on fishes and fisheries: Towards a cause-and-effect understanding. J. Fish. Biol. 77, 1745–1779 (2010).
Baumann, H. Experimental assessments of marine species sensitivities to ocean acidification and co-stressors: How far have we come?. Can. J. Zool. 97, 399–408 (2019).
Rosa, R., Rummer, J. L. & Munday, P. L. Biological responses of sharks to ocean acidification. Biol. Lett. 13, 20160796 (2017).
Heupel, M. R., Kanno, S., Martins, A. P. B. & Simpfendorfer, C. A. Advances in understanding the roles and benefits of nursery areas for elasmobranch populations. Mar. Freshw. Res. 70, 897–907 (2018).
Vinagre, C. et al. Ecological traps in shallow coastal waters—Potential effect of heat-waves in tropical and temperate organisms. PLoS ONE 13, e0192700 (2018).
Lear, K. O. et al. Thermal performance responses in free-ranging elasmobranchs depend on habitat use and body size. Oecologia 191, 829–842 (2019).
Rosa, R. et al. Early-life exposure to climate change impairs tropical shark survival. Proc. R. Soc. B 281, 20141738 (2014).
Bouyoucos, I. A. et al. Thermal tolerance and hypoxia tolerance are associated in blacktip reef shark (Carcharhinus melanopterus) neonates. J. Exp. Biol. 223, jeb221937 (2020).
Rummer, J. L., Bouyoucos, I. A., Mourier, J., Nakamura, N. & Planes, S. Responses of a coral reef shark acutely exposed to ocean acidification conditions. Coral Reefs 39, 1215–1220 (2020).
Jerde, C. L. et al. Strong evidence for an intraspecific metabolic scaling coefficient near 0.89 in fish. Front. Physiol. 10, 1166 (2019).
Green, P. & MacLeod, C. J. SIMR: An R package for power analysis of generalized linear mixed models by simulation. Methods Ecol. Evol. 7, 493–498 (2016).
Rummer, J. L., Wang, S., Steffensen, J. F. & Randall, D. J. Function and control of the fish secondary vascular system, a contrast to mammalian lymphatic systems. J. Exp. Biol. 217, 751–757 (2014).
Schwieterman, G. D. et al. Analysing tropical elasmobranch blood samples in the field: Blood stability during storage and validation of the HemoCue® haemoglobin analyser. Conserv. Physiol. 7, coz081 (2019).
Bouyoucos, I. A., Weideli, O. C., Planes, S., Simpfendorfer, C. A. & Rummer, J. L. Dead tired: Evaluating the physiological status and survival of neonatal reef sharks under stress. Conserv. Physiol. 6, coy053 (2018).
Beers, J. M. & Sidell, B. D. Thermal tolerance of Antarctic notothenioid fishes correlates with level of circulating hemoglobin. Physiol. Biochem. Zool. 84, 353–362 (2011).
Muñoz, N. J., Farrell, A. P., Heath, J. W. & Neff, B. D. Hematocrit is associated with thermal tolerance and modulated by developmental temperature in juvenile Chinook salmon. Physiol. Biochem. Zool. 91, 757–762 (2018).
Hughes, T. P. et al. Global warming and recurrent mass bleaching of corals. Nature 543, 373–377 (2017).
Baldwin, J. & Wells, R. M. G. Oxygen transport potential in tropical elasmobranchs from the Great Barrier Reef (Australia): Relationship between hematology and blood viscosity. J. Exp. Mar. Bio. Ecol. 144, 145–156 (1990).
Metcalfe, N. B., Van Leeuwen, T. E. & Killen, S. S. Does individual variation in metabolic phenotype predict fish behaviour and performance?. J. Fish. Biol. 88, 298–321 (2016).
Weideli, O. C. et al. Same species, different prerequisites: Investigating body condition and foraging success in young reef sharks between an atoll and an island system. Sci. Rep. 9, 13447 (2019).
Lear, K. O. et al. Divergent field metabolic rates highlight the challenges of increasing temperatures and energy limitation in aquatic ectotherms. Oecologia 193, 311–323 (2020).
Halsey, L. G., Killen, S. S., Clark, T. D. & Norin, T. Exploring key issues of aerobic scope interpretation in ectotherms: Absolute versus factorial. Rev. Fish Biol. Fish. 28, 405–415 (2018).
Auer, S. K., Killen, S. S. & Rezende, E. L. Resting vs. active: A meta-analysis of the intra- and inter-specific associations between minimum, sustained, and maximum metabolic rates in vertebrates. Funct. Ecol. 31, 1728–1738 (2017).
Bouyoucos, I. A., Simpfendorfer, C. A. & Rummer, J. L. Estimating oxygen uptake rates to understand stress in sharks and rays. Rev. Fish Biol. Fish. 29, 297–311 (2019).
Halsey, L. G. The reign of the p-value is over: What alternative analyses could we employ to fill the power vacuum?. Biol. Lett. 15, 20190174 (2019).
Roche, D. G., Careau, V. & Binning, S. A. Demystifying animal ‘personality’ (or not): Why individual variation matters to experimental biologists. J. Exp. Biol. 219, 3832–3843 (2016).
Bisazza, A. & Brown, C. Lateralization of cognitive functions in fish. In Fish Cognition and Behavior (eds Brown, C. et al.) 298–324 (Blackwell Publishing Ltd, New York, 2011).
Vila Pouca, C., Gervais, C., Reed, J. & Brown, C. Incubation under climate warming affects behavioral lateralisation in Port Jackson sharks. Symmetry (Basel) 10, 184 (2018).
Lear, K. O., Gleiss, A. C. & Whitney, N. M. Metabolic rates and the energetic cost of external tag attachment in juvenile blacktip sharks Carcharhinus limbatus. J. Fish. Biol. 93, 391–395 (2018).
Gleiss, A. C., Dale, J. J., Holland, K. N. & Wilson, R. P. Accelerating estimates of activity-specific metabolic rates in fishes: Testing the applicability of acceleration data-loggers. J. Exp. Mar. Bio. Ecol. 385, 85–91 (2010).
Lawrence, M. J. et al. Best practices for non-lethal blood sampling of fish via the caudal vasculature. J. Fish. Biol. 97, 4–15 (2020).
Burton, T., Killen, S. S., Armstrong, J. D. & Metcalfe, N. B. What causes intraspecific variation in resting metabolic rate and what are its ecological consequences?. Proc. R. Soc. B Biol. Sci. 278, 3465–3473 (2011).
Mourier, J. & Planes, S. Direct genetic evidence for reproductive philopatry and associated fine-scale migrations in female blacktip reef sharks (Carcharhinus melanopterus) in French Polynesia. Mol. Ecol. 22, 201–214 (2013).
Bouyoucos, I. A. et al. Home range of newborn blacktip reef sharks (Carcharhinus melanopterus), as estimated using mark-recapture and acoustic telemetry. Coral Reefs 39, 1209–1214 (2020).
Madi Moussa, R. et al. Long-term coastline monitoring on a coral reef island (Moorea, French Polynesia). Ocean Coast. Manag. 180, 104928 (2019).
Byrnes, E. E., Lear, K. O., Morgan, D. L. & Gleiss, A. C. Respirometer in a box: Development and use of a portable field respirometer for estimating oxygen consumption of large-bodied fishes. J. Fish. Biol. 96, 1045–1050 (2020).
Lear, K. O., Whitney, N. M., Brewster, L. R. & Gleiss, A. C. Treading water: Respirometer choice may hamper comparative studies of energetics in fishes. Mar. Freshw. Res. 70, 437–448 (2019).
Lear, K. O. et al. Correlations of metabolic rate and body acceleration in three species of coastal sharks under contrasting temperature regimes. J. Exp. Biol. 220, 397–407 (2017).
Watson, S.-A. et al. Ocean warming has a greater effect than acidification on the early life history development and swimming performance of a large circumglobal pelagic fish. Glob. Chang. Biol. 24, 4368–4385 (2018).
Crear, D. P. et al. The impacts of warming and hypoxia on the performance of an obligate ram ventilator. Conserv. Physiol. 7, coz026 (2019).
Pierrot, D., Lewis, E. & Wallace, D. MS Excel Program Developed for CO2 System Calculations. (2006).
Watson, S.-A., Fabricius, K. E. & Munday, P. L. Quantifying pCO2 in biological ocean acidification experiments: A comparison of four methods. PLoS ONE 12, e0185469 (2017).
Dickson, A. G., Sabine, C. L. & Christian, J. L. Guide to Best Practices for ocean CO2 Measurments Measurments (North Pacific Marine Science Organization, Sidney, 2007).
Dickson, A. G. & Millero, F. J. A comparison of the equilibrium constants for the dissociation of carbonic acid in seawater media. Deep Sea Res. Part A Oceanogr. Res. Pap. 34, 1733–1743 (1987).
Mehrbach, C., Culberson, C., Hawley, J. & Pytkowicz, R. Measurement of the apparent dissociation constants of carbonic acid in seawater at atmospheric pressure. Limnol. Ocean. 18, 897–907 (1973).
Bullock, R. W., Guttridge, T. L., Cowx, I. G., Elliott, M. & Gruber, S. H. The behaviour and recovery of juvenile lemon sharks Negaprion brevirostris in response to external accelerometer tag attachment. J. Fish. Biol. 87, 1342–1354 (2015).
Rummer, J. L., Binning, S. A., Roche, D. G. & Johansen, J. L. Methods matter: Considering locomotory mode and respirometry technique when estimating metabolic rates of fishes. Conserv. Physiol. 4, cow008 (2016).
Chabot, D., Steffensen, J. F. & Farrell, A. P. The determination of standard metabolic rate in fishes. J. Fish. Biol. 88, 81–121 (2016).
Talwar, B. et al. Validation of a portable, waterproof blood pH analyser for elasmobranchs. Conserv. Physiol. 5, cox012 (2017).
Völkel, S. & Berenbrink, M. Sulphaemoglobin formation in fish: A comparison between the haemoglobin of the sulphide-sensitive rainbow trout (Oncorhynchus mykiss) and of the sulphide-tolerant common carp (Cyprinus carpio). J. Exp. Biol. 203, 1047–1058 (2000).
Bates, D., Mächler, M., Bolker, B. & Walker, S. Fitting linear mixed-effects models using lme4. J. Stat. Softw. 67, 1215–1225 (2015).
R Core Team R: A Language and Environment for Statistical Computing (2018).
Schielzeth, H. et al. Robustness of linear mixed-effects models to violations of distributional assumptions. Methods Ecol. Evol. 11, 1141–1152 (2020).
Gelman, A. & Su, Y.-S. arm: Data analysis using regression and multilevel/hierarchical models (2018).
Support came from a JCU Postgraduate Research Scholarship, the Australian Research Council (ARC) Centre of Excellence for Coral Reef Studies, an ARC Discovery Early Career Researcher Award (PDE150101266 to J.L.R.), the Laboratoire d’Excellence “CORAIL,” the Station d’Écologie Expérimentale of the CRIOBE, and the French Ministère de l’Environnement. Thanks to Adrian Gleiss for invaluable feedback on manuscript drafts, Philip Munday and Paolo Domenici for helpful discussions, Kim Eustache for assistance in the field and lab, and volunteers and staff at the CRIOBE.
The authors declare no competing interests.
Springer Nature remains neutral with regard to jurisdictional claims in published maps and institutional affiliations.
Rights and permissions
Open Access This article is licensed under a Creative Commons Attribution 4.0 International License, which permits use, sharing, adaptation, distribution and reproduction in any medium or format, as long as you give appropriate credit to the original author(s) and the source, provide a link to the Creative Commons licence, and indicate if changes were made. The images or other third party material in this article are included in the article's Creative Commons licence, unless indicated otherwise in a credit line to the material. If material is not included in the article's Creative Commons licence and your intended use is not permitted by statutory regulation or exceeds the permitted use, you will need to obtain permission directly from the copyright holder. To view a copy of this licence, visit http://creativecommons.org/licenses/by/4.0/.
About this article
Cite this article
Bouyoucos, I.A., Watson, SA., Planes, S. et al. The power struggle: assessing interacting global change stressors via experimental studies on sharks. Sci Rep 10, 19887 (2020). https://doi.org/10.1038/s41598-020-76966-7
This article is cited by
Swimming performance of sharks and rays under climate change
Reviews in Fish Biology and Fisheries (2022)
By submitting a comment you agree to abide by our Terms and Community Guidelines. If you find something abusive or that does not comply with our terms or guidelines please flag it as inappropriate.