Advertisement
Browse Subject Areas
?

Click through the PLOS taxonomy to find articles in your field.

For more information about PLOS Subject Areas, click here.

  • Loading metrics

No maternal or direct effects of ocean acidification on egg hatching in the Arctic copepod Calanus glacialis

  • Peter Thor ,

    Roles Conceptualization, Data curation, Formal analysis, Funding acquisition, Investigation, Methodology, Project administration, Resources, Supervision, Validation, Visualization, Writing – original draft

    peter.thor@npolar.no

    Affiliation Norwegian Polar Institute, Fram Centre, Tromsø, Norway

  • Fanny Vermandele,

    Roles Conceptualization, Formal analysis, Investigation, Methodology, Writing – original draft, Writing – review & editing

    Affiliation Université du Québec à Rimouski, Département de Biologie Chimie et Géographie, Rimouski, Canada

  • Marie-Helene Carignan,

    Roles Conceptualization, Formal analysis, Investigation, Methodology, Writing – original draft, Writing – review & editing

    Affiliation Université du Québec à Rimouski, Département de Biologie Chimie et Géographie, Rimouski, Canada

  • Sarah Jacque,

    Roles Formal analysis, Investigation, Methodology, Writing – original draft

    Affiliation Université du Québec à Rimouski, Département de Biologie Chimie et Géographie, Rimouski, Canada

  • Piero Calosi

    Roles Conceptualization, Data curation, Formal analysis, Funding acquisition, Investigation, Methodology, Resources, Supervision, Validation, Visualization, Writing – original draft, Writing – review & editing

    Affiliation Université du Québec à Rimouski, Département de Biologie Chimie et Géographie, Rimouski, Canada

No maternal or direct effects of ocean acidification on egg hatching in the Arctic copepod Calanus glacialis

  • Peter Thor, 
  • Fanny Vermandele, 
  • Marie-Helene Carignan, 
  • Sarah Jacque, 
  • Piero Calosi
PLOS
x

Abstract

Widespread ocean acidification (OA) is transforming the chemistry of the global ocean and the Arctic is recognised as the region where this transformation will occur at the fastest rate. Moreover, many Arctic species are considered less capable of tolerating OA due to their lower capacity for acid-base regulation. This inability may put severe restraints on many fundamental functions, such as growth and reproductive investments, which ultimately may result in reduced fitness. However, maternal effects may alleviate severe effects on the offspring rendering them more tolerant to OA. In a highly replicated experiment we studied maternal and direct effects of OA predicted for the Arctic shelf seas on egg hatching time and success in the keystone copepod species Calanus glacialis. We incubated females at present day conditions (pHT 8.0) and year 2100 extreme conditions (pHT 7.5) during oogenesis and subsequently reciprocally transplanted laid eggs between these two conditions. Statistical tests showed no effects of maternal or direct exposure to OA at this level. We hypothesise that C. glacialis may be physiologically adapted to egg production at low pH since oogenesis can also take place at conditions of potentially low haemolymph pH of the mother during hibernation in the deep.

Introduction

Uptake of anthropogenic CO2 is changing the chemistry of the global ocean [1]. When entering the sea, CO2 reacts with water to form carbonic acid, and this ocean acidification (OA) has lowered the global ocean mean surface pH from 8.13 during the pre-industrial age to the present day 8.05. This trend is predicted to continue and current models estimate a further decrease of up to 0.4 pH units by the year 2100 [24]. In this respect, the Arctic is a region of specific concern. OA is currently progressing at faster rates in many Arctic regions and is expected to continue to do so [1, 57]. This is partly due to rising temperatures generating increasing volumes of sea ice melt water, which holds low H+ buffering capacity [8]. Moreover, while the Arctic Ocean contains only 1% of the global ocean volume, it receives 11% of the global riverine discharge. This discharge not only carries low H+ buffering capacity but also contributes significant loads of terrestrial carbon, which increases CO2 production by promoting heterotrophic microbial respiration [9]. Finally, inflow from the North Atlantic transports increasing amounts of anthropogenic CO2 to the Arctic Ocean [10]. Arctic organisms are therefore the first to face the effects of OA and will continue to experience stronger OA in the future [7].

The magnitude of these changes extends beyond anything experienced during most species’ evolutionary history [11], and while significant effects are predicted for many marine animals [12, 13], effects may be particularly conspicuous in the Arctic. Contrary to lower latitude eurythermal animals, true Polar species show low energetic costs for physiological maintenance at low temperatures [14, 15]. This is, however, at the expense of a lower capacity for cellular homeostasis and acid-base regulation [16]. The capacity to counter negative effects of OA is therefore thought to be particularly low in Arctic species. Moreover, while direct effects from the immediate environment will impose serious implications for sensitive organisms, effects carried through the generations may convey either alleviation or additional stress. Adaptation will enable increased tolerance to a changed environment [17], while maternal effects carried to the offspring may act in either direction. Maternal effects can precondition offspring to the environment experienced by mothers through cytoplasmic and mitochondrial factors packaged into the egg during oogenesis [1821]. However, under severe maternal stress these factors may be lacking or differently conditioned resulting in poorly developing offspring. For instance, copepods mothers’ ingestion of low quality prey including harmful diatoms have shown detrimental effects on egg hatching and subsequent naupliar development [2224]. Such changes may have far-reaching consequences, and a depression of the long term year-to-year recruitment of nauplii larvae or a delay in the timing of this recruitment can have significant effects on the population development [25]. When these effects occur in ecologically important species, they may spread beyond the species itself.

Calanus glacialis constitutes a keystone species in the Arctic Ocean and adjacent seas [2628]. Along the continental shelf this species dominates in terms of biomass, may exert significant grazing pressure on microplankton prey, and is a very important food item for many pelagic predators such as carnivorous copepods and amphipods, but also Arctic fish species, baleen whales, and marine birds [2931]. Any changes to C. glacialis production will therefore extend beyond the copepods themselves and potentially encompass a larger part of the entire food web. As a consequence, much attention has been given C. glacialis and its possible future in a changing Arctic [3236].

In the present study, we investigated the effects of the immediate and maternal pH environment as predicted for the Arctic Ocean in year 2100 [1] on egg hatching dynamics in C. glacialis. Egg hatching success (EHS) is not the only determinant, besides egg production rate, of population recruitment success. Copepod eggs are often subjected to high mortality rates [3739], and while decreased EHS would have direct consequences for population recruitment, any delay in the timing of egg hatching will increase individual predation risk. Moreover, delayed hatching may increase the risk of phenological miss-match with the succession of the phytoplankton bloom rendering the developing larvae less adequately nourished [25]. We therefore investigated the effects of OA on both EHS and egg hatching time. Differentiation between maternal and direct effects was accomplished by reciprocally transplanting eggs produced by females subjected to high and low pH. Calanus glacialis show both capital and income breeding strategies [40, 41], so the study period was chosen late in spring to avoid contribution from the winter energy capital and increase the possibility that all energy for egg production was obtained from ingested food during the OA incubation.

Methods

Collection of copepods

Calanus glacialis were caught by vertical tows, 100 m to the surface, with a 200 μm WP2 plankton net (KC Research equipment, Silkeborg, Denmark) with a closed cod end in the Kongsfjord, Svalbard (79.0° N, 11.7° E) in late May 2016. No specific authorisation was needed for collecting copepods, and no endangered species were involved. On deck, the content of the cod end was diluted in 25 L sea water produced from water collected at 80 m. Copepods were then transported to a cold room (5°C) at the nearby Kings Bay Marine Laboratory (Ny-Ålesund, Svalbard). Calanus glacialis females were selected under the stereoscope using cut off plastic Pasteur pipettes keeping all vessels on ice to avoid high temperatures. Individuals were identified to species by number of pleopods and abdominal segments. They were distinguished from C. finmarchicus and C. hyperboreus on the basis of size [28], the presence of red pigmentation in the antennules, a characteristic distinguishing C. glacialis from C. finmarchicus [42], and the lack of lateral spikes on the distal prosome segment, which is a characteristic of C. hyperboreus. Several hundred females were collected in a 50 L bucket to be distributed into incubation buckets.

Preparation of incubation water

For the initiation of incubations six 50 L buckets were filled with 0.3 μm filtered sea water obtained from a seawater intake at 80 m depth (fsw). For the low pH treatment, small volumes of fsw acidified to ca. pHNBS 5.5 (National Bureau of Standards scale) by CO2 bubbling (Mapcon CO2, Yara Praxair, Tromsø, Norway) were mixed into three of these buckets to reach a target pHNBS of 7.5 as measured by a Metrohm 826 pH meter equipped with a Metrohm LL aquatrode electrode. Total scale pH (pHT) was determined spectrophotometrically in 12 mL water samples pipetted in 5 cm quartz cuvettes. Absorbance was measured at 578 nm, 434 nm, and 730 nm using a UV-2401PC spectrophotometer (UV-2401PC, Shimadzu Inc., Kyoto, Japan) after addition of 10 μL of m-cresol-purple. pHT was then calculated according to Clayton and Burne [43] with a dye-addition correction [44] and adjusted from measurement temperature to in situ temperature according to Gieskes [45]. We did not measure a second carbonate chemistry variable as in our previous OA studies [17, 32, 33, 4649], and we were unable to calculate the full carbonate chemistry, which is otherwise recommended [50].

For food, paste of the diatom Thalassiosira weissflogii (Tw 1200, Reed Mariculture, Campbell, CA, USA) was added to a final concentration of ca. 10 μg Chl a L-1. Prior to the experiment, the necessary dilution of the algal paste was established from the Chl a content of a 100x dilution of the algal paste determined using a spectrophotometer (UV-2401PC, Shimadzu Inc.) after overnight extraction in 70% ethanol [51]. Cell concentrations in this dilution was established by cell counts under the microscope in a Bürker-Türk counting chamber. The suitability of the algal paste as prey for C. glacialis had been assured previously by comparing faecal pellets counts from incubations of copepods with counts from copepods incubated at similar concentrations of live T. weissflogii (Peter Thor, pers. comm.).

Copepod and egg incubations

Collected C. glacialis females were released into 30 L of fsw, which was divided in six by volume. Copepods from these six batches were then caught on a 200 μm filter and re-introduced immediately into the six incubation buckets. This started the 7 d incubation of the females. No additional females were added during those 7 days. The water was kept in motion by gentle bubbling and turned once every day to keep algal food in suspension. Ingestion was ascertained by frequent observations of the copepods’ gut colour.

After incubating for 7 d, all eggs were removed from the bottom of the buckets by siphoning and the next day, all eggs produced from day 7 to day 8 were collected from each bucket, also by siphoning. These eggs were collected on a 50 μm mesh size sieve, divided in two and re-suspended in pre-prepared high and low pH incubation water in two 500 mL pitchers. From each of these pitchers, eggs were distributed by volume into nine replicate 50 mL flat cell culture flasks (VWR Collection, Darmstadt, Germany) equipped with 50 μm mesh in the caps to allow exchange with the outside water (total of 2 pH levels x 9 replicates x 6 buckets = 108 flasks). These flasks were then transplanted from the origin bucket to all six incubation buckets according to the design in Fig 1 for the remainder of the experiment. The flask received on average 21 ± 9 eggs (mean ± SD). Eggs were counted twice every day directly in the flasks under a stereomicroscope until the fourth day after which they were counted once every day. Eggs where clearly visible through the flask walls.

thumbnail
Fig 1. Transplants of eggs among incubation buckets.

For clarity only transplants in one treatment group (High to low pH; HL) are shown. The table shows all transplants for each treatment group. Three flasks with eggs were transplanted along each of the arrows in the figure. In total, each treatment group contained nine transplants.

https://doi.org/10.1371/journal.pone.0192496.g001

pHT was monitored as above once every day in all buckets, and when necessary, the water was renewed by inserting a large 200 μm sieve into the water and siphoning off approximately 3/4 of the water in the bucket from inside of this sieve and replacing it with newly prepared water. Algal concentration were measured by cell counts once every day and algae were added to maintain target concentrations.

Data treatment and statistical analyses

For each flask, number of remaining eggs was converted to fraction hatched at every sampling event. Egg hatching success (EHS) was calculated as the mean of fraction hatched from the last three sampling events. To investigate possible delay effects of pHT in hatching, a sigmoid Hill function was fitted to the cumulative increase in fraction hatched eggs over time in each flask. The Hill function outputs values of average time to hatching (Km) and maximum egg hatching (E): , where ê is predicted fraction hatched at time t and h is the sigmoid inflexion factor. After removal of outliers (values further than two standard deviations from the median), values of EHS and Km (interpreted as average time to hatching) were compared among the four treatment groups (high to high pH, high to low pH, low to high pH, and low to low pH) by 1-factor permutational analysis of variance (PERMANOVA) on similarity matrices assembled using Euclidian distances in Primer 6+ [52] employing a nested PERMANOVA design: Treatment group + transplants(treatment group), where “transplants” were the specific transplants among the treatment groups (i.e. the arrows in Fig 1).

Average water temperature and pHT throughout the incubation period were compared among incubation buckets by 1-factor PERMANOVA on similarity matrices assembled using Euclidian distances.

All PERMANOVA tests were followed by PERMDISP tests to verify the assumption of homogeneity of multivariate dispersions.

Results

There were no significant differences in average temperature among the incubation buckets during the incubation period (Table 1; 1-factor PERMANOVA: Pseudo-F5,71 = 0.18, P = 0.98). pHT differed significantly between high and low pH treatments and there were no significant difference among buckets within treatments (1-factor PERMANOVA pair-wise tests: P > 0.05). There were no significant differences in diatom food concentration among buckets (1-factor PERMANOVA: Pseud-F5,59 = 0.29, P = 0.91).

thumbnail
Table 1. Averages of temperature (T), total scale pH (pHT), salinity (S), and algal concentration during the incubation period.

https://doi.org/10.1371/journal.pone.0192496.t001

In general egg hatching took place two days after collection of eggs from the bucket floors (Fig 2). There were no significant differences in average time to hatching (Km) nor was there any significant confounding effects from the nested transplant factor (1-factor PERMANOVA: Treatment group: Pseudo-F3,93 = 0.70, P = 0.55, transplant(treatment group) Pseudo-F32,93 = 1.61, P = 0.057) (Table 2). Furthermore, there were no significant difference among the four treatment groups in egg hatching success (EHS) (1-factor PERMANOVA: Treatment group: Pseudo-F3,93 = 0.44, P = 0.72, transplant (treatment group) Pseudo-F32,93 = 0.99, P = 0.51) (Table 2).

thumbnail
Fig 2. Cumulative egg hatching during the incubation period.

To enable comparison among flasks holding different initial numbers of eggs, egg counts were calculated as fractions of the number of eggs at the first count. Solid lines show mean predicted values from the Hill regressions on each individual flask. The vertical lines at t = 2 d is inserted as a guide to facilitate visual judgement of differences among treatments.

https://doi.org/10.1371/journal.pone.0192496.g002

thumbnail
Table 2. Egg hatching success (EHS) and average time to hatching (Km) in the four treatments.

Means ± standard deviations. Values of Km are means of individual regressions on cumulative hatching from each incubation flask.

https://doi.org/10.1371/journal.pone.0192496.t002

All raw data on egg hatching are submitted in the supporting S1 Table.

Discussion

In the study presented here, we did not detect any significant direct or maternally transferred effects of pH levels predicted for the Arctic Ocean in year 2100 on egg hatching success (EHS) or egg hatching timing (Km) of Calanus glacialis eggs.

Effects of pH on EHS has been studied previously in different Calanus species. In C. glacialis egg hatching success was lower at pHNBS 6.9 [36], whereas pH levels more closely mimicking Arctic Ocean predictions for the year 2100 (pHNBS 7.6) left EHS unchanged, although high variation within treatments may have masked effects [36]. When subjecting C. finmarchicus females and eggs to pHNBS 6.95, EHS was strongly reduced [53], but in the congener C. helgolandicus EHS did not change when subjecting the copepods to pHNBS 7.75 [54]. Considering other calanoid genera, the picture looks somewhat different. EHS was significantly lowered in Acartia clausi at pHT 7.83 compared to pHT 8.03 [55]. Similarly, in Acartia tonsa EHS was significantly lowered already at pHNBS 7.81 [56]. However, the copepods for the A. tonsa study were obtained from commercial cultures in which the carbonate chemistry may be different than in the wild. It may well be that copepods from such cultures could be adapted to an environment with only minor chemical variations and therefore would respond stronger to pH changes. In Acartia steueri, EHS was significantly depressed at pH 7.3 (no pH scale indicated) when comparing effects through three generations [57]. However, when trying to extract specific information on the effects of long term multigenerational exposure the significant difference disappeared, although this may have been due to low statistical power. A study of OA effects on complete pelagic communities from the Baltic Sea revealed significant negative effects of low pH (pH 7.45) on EHS [58, 59]. Interestingly, by transplanting eggs between low and high pH environments, Vehmaa and colleagues showed that maternal effects can alleviate pH effects on EHS but only at moderately reduced pH [58]. Eggs from females exposed to moderately reduced pH experienced significantly higher EHS compared to eggs produced by non-exposed females, contrary to what we observed in C. glacialis. Also, decreased pH may act to change the egg hatching response to increasing water temperature. In Acartia sp., low pH reduced the positive effect of increased temperature on EHS [60]. On the other hand, this interacting effect was not seen in A. clausi where low pH reduced EHS at both high and low temperature [55]. There is no calcification in the copepod exoskeleton and OA effects are carried to copepods foremost by changes in hemolymph pH. Consequently, and because of logistical constraints, we did not measure a second carbonate chemistry variable to enable calculation of the full chemistry. Nevertheless, alkalinity is mostly stable and intermediate in the Kongsfjord [61] and we expect no extremes of carbonate chemistry at the time of the experiments.

We studied egg hatching in C. glacialis despite the previous findings that EHS are not influenced by pH levels similar to the present study [36] because EHS is not the only determinant of population recruitment success. Copepods experience widely different predation risk through their life cycle. Eggs and young nauplii larvae constitute important prey for pelagic predators and consequently they experience high mortality rates [3739]. Older nauplii and copepodite stages possess more efficient behavioural escape mechanisms which lessen size dependent predation risk [62, 63]. Thus, while decreased EHS would have direct consequences for population recruitment, any temporal delay in the timing of egg hatching or development in the young stages is equally detrimental since it increases individual life-time predation risk. Moreover, and perhaps more importantly, delayed hatching and development may increase the risk of phenological miss-match with the succession of the phytoplankton bloom [25]. Although C. glacialis shows capital breeding in the ice-free Kongsfjord, they rely on the relatively short ice algal and later pelagic phytoplankton blooms for the production of larvae in most of the Arctic [41]. While increasing temperatures may at least partially remove the ice algal bloom, they also shifts the pelagic bloom to occur earlier in the season. Copepods experience the same shift, but it not as pronounced resulting in a temporal trophic miss-match, which impairs optimal exploitation of the bloom [25]. Obviously, any delay in egg hatching by OA would only accentuate this miss-match. Hatching rate has been shown to be significantly impaired already at pHT 7.75 in Pseudocalanus acuspes [49]. Also, studies on Acartia sp. have shown significant delay of egg hatching at low pH [60]. However, a closer look at the Vehmaa et al. data [60] reveals that samples were not taken simultaneously around Km for the different treatments. This non-simultaneous sampling may have biased results and there could be a risk that differences in the sigmoid accumulation of hatched eggs among treatments emerged as an artefact.

Effects of OA levels predicted for year 2100 on egg hatching seem to be lower in larger than smaller calanoid copepods. Such difference could arise from differences in the sensitivity of energy allocation to OA between the two groups. For instance, energetic expenses of growth seems to increase at decreasing pH in female P. acuspes [48], and a recent study indicated that this may also be true for C. glacialis stage IV copepodites [46]. On the other hand, a lack of similar effects in stage V copepodites in that same study showed that effects may be stage dependant and adult females may respond differently [46]. Alternatively, the differences may stem from differences in ontogeny. Copepods of the large Calanus genus undergo ontogenetic vertical migration and winter hibernation in the deep. During such overwintering, the copepods experience haemolymph pH possibly as low as 5.5 as a result of metabolic depression during hibernation [64]. C. glacialis is an opportunistic capital breeder and production of the first eggs of the season often takes place in the deep [41]. It is therefore quite conceivable that mechanisms to counter low pH could have evolved to protect early oogenesis. Later in the season, eggs are predominately produced on ingested energy (income breeding) [40, 41]. Broader support for the idea that taxa living under different pH regimes have evolved different physiologies has been found also in pteropods and polychaetes [6568].

Naupliar growth and development is similarly unaffected and it seems that C. glacialis will develop from oviposition to the first copepodite stage unaffected under the future OA scenario tested here [33]. Consequently, OA will not alter the exposure to early life predation mortality or introduce any phenological miss-match with phytoplankton bloom timing. Similarly, larval growth and development of the congener C. finmarchicus is equally unaffected which adds strength to the argument that naupliar recruitment and development in the Calanus genus is generally unaffected by OA [69].

Supporting information

S1 Table. Raw values of unhatched eggs remaining versus time.

The first sheet, “info”, contains information on the ordering of the buckets and replicate flasks in the data sheets. Data sheets are arranged according to target buckets in the transplant (H meaning high pH and L meaning low pH). In each sheet the first column shows origin bucket label, the second column shows target bucket label, and the following columns show time (d) and number of unhatched eggs remaining at each sampling event.

https://doi.org/10.1371/journal.pone.0192496.s001

(XLSX)

Acknowledgments

We thank the staff at the Kings Bay Marine Lab, Ny-Ålesund for their invaluable technical assistance and the staff at the Sverdrup Station, Ny-Ålesund for logistic support.

References

  1. 1. Hoegh-Guldberg O, Cai R, Poloczanska ES, Brewer PG, Sundby S, Hilmi K, et al. The Ocean. In: Barros VR, Field CB, Dokken DJ, Mastrandrea MD, Mach KJ, Bilir TE, et al., editors. Climate Change 2014: Impacts, Adaptation, and Vulnerability Part B: Regional Aspects Contribution of Working Group II to the Fifth Assessment Report of the Intergovernmental Panel of Climate Change. Cambridge, United Kingdom and New York, NY, USA: Cambridge University Press; 2014. p. 1655–731.
  2. 2. Bopp L, Resplandy L, Orr JC, Doney SC, Dunne JP, Gehlen M, et al. Multiple stressors of ocean ecosystems in the 21st century: projections with CMIP5 models. Biogeosciences. 2013; 10(10): 6225–45.
  3. 3. Caldeira K, Wickett ME. Ocean model predictions of chemistry changes from carbon dioxide emissions to the atmosphere and ocean. Journal of Geophysical Research-Oceans. 2005; 110(C9): C09S4.
  4. 4. Cao L, Caldeira K, Jain AK. Effects of carbon dioxide and climate change on ocean acidification and carbonate mineral saturation. Geophysical Research Letters. 2007; 34(5): L05607.
  5. 5. Fabry VJ, McClintock JB, Mathis JT, Grebmeier JM. Ocean acidification at high latitudes: The bellweather. Oceanography. 2009; 22(4): 160–71.
  6. 6. Steinacher M, Joos F, Frölicher TL, Plattner GK, Doney SC. Imminent ocean acidification in the Arctic projected with the NCAR global coupled carbon cycle-climate model. Biogeosciences. 2009; 6(4): 515–33.
  7. 7. AMAP. AMAP Assessment 2013: Arctic Ocean acidification. Oslo: Arctic Monitoring and Assessment Programme; 2013.
  8. 8. Yamamoto-Kawai M, McLaughlin FA, Carmack EC, Nishino S, Shimada K. Aragonite Undersaturation in the Arctic Ocean: Effects of Ocean Acidification and Sea Ice Melt. Science. 2009; 326(5956): 1098–100. pmid:19965425
  9. 9. Raymond PA, McClelland JW, Holmes RM, Zhulidov AV, Mull K, Peterson BJ, et al. Flux and age of dissolved organic carbon exported to the Arctic Ocean: A carbon isotopic study of the five largest arctic rivers. Global Biogeochemical Cycles. 2007; 21(4): GB4011.
  10. 10. Fransson A, Chierici M, Anderson LG, Bussmann I, Kattner G, Peter Jones E, et al. The importance of shelf processes for the modification of chemical constituents in the waters of the Eurasian Arctic Ocean: implication for carbon fluxes. Cont Shelf Res. 2001; 21(3): 225–42.
  11. 11. Fabry VJ, Seibel BA, Feely RA, Orr JC. Impacts of ocean acidification on marine fauna and ecosystem processes. ICES J Mar Sci. 2008; 65(3): 414–32.
  12. 12. Wittmann AC, Pörtner HO. Sensitivities of extant animal taxa to ocean acidification. Nature Climate Change. 2013; 3(11): 995–1001.
  13. 13. Dupont S, Pörtner HO. Get ready for ocean acidification. Nature. 2013; 498(7455): 429–. pmid:23803827
  14. 14. Clarke A. A reappraisal of the concept of metabolic cold adaptation in polar marine invertebrates. Biol J Linn Soc. 1980; 14(1): 77–92.
  15. 15. Rastrick SP, Whiteley NM. Congeneric amphipods show differing abilities to maintain metabolic rates with latitude. Physiol Biochem Zool. 2011; 84(2): 154–65. pmid:21460526
  16. 16. Pörtner H-O. Oxygen- and capacity-limitation of thermal tolerance: a matrix for integrating climate-related stressor effects in marine ecosystems. J Exp Biol. 2010; 213(6): 881–93. pmid:20190113
  17. 17. De Wit P, Dupont S, Thor P. Selection on oxidative phosphorylation and ribosomal structure as a multigenerational response to ocean acidification in the common copepod Pseudocalanus acuspes. Evol Appl. 2015; 9: 1112–23. pmid:27695519
  18. 18. Mousseau TA, Fox CW. The adaptive significance of maternal effects. Trends Ecol Evol. 1998; 13(10): 403–7. pmid:21238360
  19. 19. Bernardo J. Maternal Effects in Animal Ecology. Am Zool. 1996; 36(2): 83–105.
  20. 20. Wolf JB, Wade MJ. What are maternal effects (and what are they not)? Philosophical Transactions of the Royal Society B: Biological Sciences. 2009; 364(1520): 1107–15.
  21. 21. Davidson EH. Gene activity in early development New York: Academic Press; 1976 468 p.
  22. 22. Ianora A, Poulet SA, Miralto A. The effects of diatoms on copepod reproduction: a review. Phycologia. 2003; 42(4): 351–63.
  23. 23. Romano G, Russo GL, Buttino I, Ianora A, Miralto A. A marine diatom-derived aldehyde induces apoptosis in copepod and sea urchin embryos. J Exp Biol. 2003; 206(Pt 19): 3487–94. pmid:12939379
  24. 24. Thor P, Koski M, Tang KW, Jónasdóttir SH. Supplemental effects of diet mixing on absorption of ingested organic carbon in the marine copepod Acartia tonsa. Mar Ecol Prog Ser. 2007; 331: 131–8.
  25. 25. Edwards M, Richardson AJ. Impact of climate change on marine pelagic phenology and trophic mismatch. Nature. 2004; 430(7002): 881–4. pmid:15318219
  26. 26. Mumm N, Auel H, Hanssen H, Hirche HJ. Breaking the ice: large-scale distribution of mesozooplankton after a decade of Arctic and transpolar cruises. Polar Biol. 1998; 20: 189–97.
  27. 27. Weydmann A, Coelho NC, Serrão EA, Burzyński A, Pearson GA. Pan-Arctic population of the keystone copepod Calanus glacialis. Polar Biol. 2016: 1–8.
  28. 28. Arnkværn G, Daase M, Eiane K. Dynamics of coexisting Calanus finmarchicus, Calanus glacialis and Calanus hyperboreus populations in a high-Arctic fjord. Polar Biol. 2005; 28(7): 528–38.
  29. 29. Lowry L. Foods and feeding ecology. In: Montague JJ, Cowles CJ, editors. Bowhead whales. Lawrence, KS: Society of Marine Mammalogy, Allen Press.; 1993.
  30. 30. Karnovsky NJ, Kwaśniewski S, Węsławski JM, Walkusz W, Beszczyńska-Möller A. Foraging behavior of little auks in a heterogeneous environment. Mar Ecol Prog Ser. 2003; 253: 289–303.
  31. 31. Hop H, Gjøsæter H. Polar cod (Boreogadus saida) and capelin (Mallotus villosus) as key species in marine food webs of the Arctic and the Barents Sea. Mar Biol Res. 2013; 9(9): 878–94.
  32. 32. Thor P, Bailey A, Halsband C, Guscelli E, Gorokhova E, Fransson A. Seawater pH predicted for the year 2100 affects the metabolic response to feeding in copepodites of the Arctic copepod Calanus glacialis. PLoS ONE. 2016; 11(12): e0168735. pmid:27992579
  33. 33. Bailey A, Thor P, Browman HI, Fields DM, Runge J, Vermont A, et al. Early life stages of the Arctic copepod Calanus glacialis are unaffected by increased seawater pCO2. ICES J Mar Sci. 2016; 74: 996–105.
  34. 34. Hildebrandt N, Sartoris FJ, Schulz KG, Riebesell U, Niehoff B. Ocean acidification does not alter grazing in the calanoid copepods Calanus finmarchicus and Calanus glacialis. ICES J Mar Sci. 2016; 73(3): 927–36.
  35. 35. Hildebrandt N, Niehoff B, Sartoris FJ. Long-term effects of elevated CO2 and temperature on the Arctic calanoid copepods Calanus glacialis and C. hyperboreus. Mar Pollut Bull. 2014; 80(1–2): 59–70. pmid:24529340
  36. 36. Weydmann A, Søreide JE, Kwasniewski S, Widdicombe S. Influence of CO2-induced acidification on the reproduction of a key Arctic copepod Calanus glacialis. J Exp Mar Biol Ecol. 2012; 428: 39–42.
  37. 37. Sell AF, van Keuren D, Madin LP. Predation by omnivorous copepods on early developmental stages of Calanus finmarchicus and Pseudocalanus spp. Limnol Oceanogr. 2001; 46(4): 953–9.
  38. 38. Bonnet D, Titelman J, Harris R. Calanus the cannibal. J Plankton Res. 2004; 26(8): 937–48.
  39. 39. Eiane K, Ohman MD. Stage-specific mortality of Calanus finmarchicus, Pseudocalanus elongatus and Oithona similis on Fladen Ground, North Sea, during a spring bloom. Mar Ecol Prog Ser. 2004; 268: 183–93.
  40. 40. Niehoff B. Life history strategies in zooplankton communities: The significance of female gonad morphology and maturation types for the reproductive biology of marine calanoid copepods. Prog Oceanogr. 2007; 74(1): 1–47.
  41. 41. Daase M, Falk-Petersen S, Varpe Ø, Darnis G, Søreide JE, Wold A, et al. Timing of reproductive events in the marine copepod Calanus glacialis: a pan-Arctic perspective. Can J Fish Aquat Sci. 2013; 70(6): 871–84.
  42. 42. Nielsen TG, Kjellerup S, Smolina I, Hoarau G, Lindeque P. Live discrimination of Calanus glacialis and C. finmarchicus females: can we trust phenological differences? Mar Biol. 2014; 161(6): 1299–306.
  43. 43. Clayton TD, Byrne RH. Spectrophotometric seawater pH measurements: total hydrogen ion concentration scale calibration of m-cresol purple and at-sea results. Deep Sea Research Part I: Oceanographic Research Papers. 1993; 40(10): 2115–29.
  44. 44. Dickson AG, Sabine CL, Christian JR. Guide to best practices for ocean CO2 measurements. Sidney, BC, Canada.: PICES; 2007.
  45. 45. Gieskes JM. Effects of temperature on the pH of seawater. Limnol Oceanogr. 1969; 14(5): 679–85.
  46. 46. Thor P, Bailey A, Dupont S, Calosi P, Søreide JE, De Wit P, et al. Contrasting physiological response to future ocean acidification among Arctic copepod population. Glob Change Biol. 2018; 24: e365–e77.
  47. 47. Bailey A, De Wit P, Thor P, Browman H, Bjelland R, Shema S, et al. Regulation of gene expression underlies tolerance of the Arctic copepod Calanus glacialis to CO2-acidified water. Ecology and Evolution. 2017.
  48. 48. Thor P, Oliva EO. Ocean acidification elicits different energetic responses in an Arctic and a boreal population of the copepod Pseudocalanus acuspes. Mar Biol. 2015; 162: 799–807.
  49. 49. Thor P, Dupont S. Transgenerational effects alleviate severe fecundity loss during ocean acidification in a ubiquitous planktonic copepod. Glob Change Biol. 2015; 21: 2261–71.
  50. 50. Riebesell U, Fabry VJ, Hansson L, Gattuso JP. Guide to best practice for research for ocean acidification and data reporting. Luxembourg: Publications Office of the European Union; 2010.
  51. 51. Strickland JD, Parsons TR. A practical handbook of seawater analysis. Journal of the Fisheries Research Board of Canada. 1972; 167: 310.
  52. 52. Anderson MJ. A new method for non-parametric multivariate analysis of variance. Austral Ecol. 2001; 26(1): 32–46.
  53. 53. Mayor DJ, Matthews C, Cook K, Zuur AF, Hay S. CO2-induced acidification affects hatching success in Calanus finmarchicus. Mar Ecol Prog Ser. 2007; 350: 91–7.
  54. 54. Mayor DJ, Everett NR, Cook KB. End of century ocean warming and acidification effects on reproductive success in a temperate marine copepod. J Plankton Res. 2012; 34(3): 258–62.
  55. 55. Zervoudaki S, Frangoulis C, Giannoudi E, Krasakopoulou E. Effects of low pH and raised temperature on egg production, hatching and metabolic rates of a Mediterranean copepod species (Acartia clausi) under oligotrophic conditions. Mediterr Mar Sci. 2014; 15: 74–83.
  56. 56. Cripps G, Lindeque P, Flynn KJ. Have we been underestimating the effects of ocean acidification in zooplankton? Glob Change Biol. 2014; 20: 3377–85.
  57. 57. Kurihara H, Ishimatsu A. Effects of high CO2 seawater on the copepod (Acartia tsuensis) through all life stages and subsequent generations. Mar Pollut Bull. 2008; 56(6): 1086–90. pmid:18455195
  58. 58. Vehmaa A, Almén A-K, Brutemark A, Paul A, Riebesell U, Furuhagen S, et al. Ocean acidification challenges copepod reproductive plasticity. Biogeosciences Discussions. 2015; 12(22): 18541–70.
  59. 59. Paul AJ, Bach LT, Schulz KG, Boxhammer T, Czerny J, Achterberg EP, et al. Effect of elevated CO2 on organic matter pools and fluxes in a summer Baltic Sea plankton community. Biogeosciences. 2015; 12(20): 6181–203.
  60. 60. Vehmaa A, Brutemark A, Engstrom-Ost J. Maternal effects may act as an adaptation mechanism for copepods facing pH and temperature changes. PLoS ONE. 2012; 7(10): e48538. pmid:23119052
  61. 61. Fransson A, Chierici M, Hop H, Findlay HS, Kristiansen S, Wold A. Late winter-to-summer change in ocean acidification state in Kongsfjorden, with implications for calcifying organisms. Polar Biol. 2016: 1–17.
  62. 62. Titelman J, Kiørboe T. Predator avoidance by nauplii. Mar Ecol Prog Ser. 2003; 247: 137–49.
  63. 63. Thor P, Nielsen TG, Tiselius P. Mortality rates of epipelagic copepods in the post-spring bloom period in the Disko Bay, western Greenland. Mar Ecol Prog Ser. 2008; 359: 151–60.
  64. 64. Freese D, Niehoff B, Søreide JE, Sartoris FJ. Seasonal patterns in extracellular ion concentrations and pH of the Arctic copepod Calanus glacialis. Limnol Oceanogr. 2015; 60(6): 2121–9.
  65. 65. Maas AE, Wishner KF, Seibel BA. The metabolic response of pteropods to acidification reflects natural CO2-exposure in oxygen minimum zones. Biogeosciences. 2012; 9(2): 747–57.
  66. 66. Calosi P, Rastrick SPS, Lombardi C, de Guzman HJ, Davidson L, Jahnke M, et al. Adaptation and acclimatization to ocean acidification in marine ectotherms: an in situ transplant experiment with polychaetes at a shallow CO2 vent system. Philosophical Transactions of the Royal Society B: Biological Sciences. 2013; 368(1627): 20120444.
  67. 67. Turner LM, Ricevuto E, Massa-Gallucci A, Gambi M-C, Calosi P. Energy metabolism and cellular homeostasis trade-offs provide the basis for a new type of sensitivity to ocean acidification in a marine polychaete at a high-CO2 vent: adenylate and phosphagen energy pools versus carbonic anhydrase. J Exp Biol. 2015; 218(14): 2148–51.
  68. 68. Turner LM, Ricevuto E, Gallucci AM, Lorenti M, Gambi M-C, Calosi P. Metabolic responses to high pCO2 conditions at a CO2 vent site in juveniles of a marine isopod species assemblage. Mar Biol. 2016; 163(10): 211. pmid:27729710
  69. 69. Runge JA, Fields DM, Thompson CRS, Shema SD, Bjelland RM, Durif CMF, et al. End of the century CO2 concentrations do not have a negative effect on vital rates of Calanus finmarchicus, an ecologically critical planktonic species in North Atlantic ecosystems. ICES J Mar Sci. 2016; 73(3): 937–50.