Sunday , October 24 2021

Northern cod species face habitat losses if global warming exceeds 1.5 ° C



Rapid climate change in the Northeast Atlantic and Arctic poses a threat to some of the world's largest fish populations. Impacts of warming and acidification may become accessible through mechanism-based risk assessments and projections of future habitat suitability. We show that ocean acidification causes a narrowing of embryonic thermal ranges, which identifies the suitability of spawning habitats as a critical life-history bottleneck for two abundant cod species. Embryonic tolerances linked to climate simulations reveal that ever-increasing CO2 emissions [Representative Concentration Pathway (RCP) 8.5] will deteriorate the suitability of present spawning habitat for both Atlantic cod (Gadus morhua) and Polar cod (Boreogadus saida) by 2100. Moderate warming (RCP4.5) may avert a hazardous climate impact on Atlantic cod but still leaves few spawning areas for the more vulnerable Polar cod, which also loses the benefits of an ice-covered ocean. Emissions following RCP2.6, however, support largely unchanged habitability for both species, suggesting that risks are minimized if warming is held "below 2 ° C, if not 1.5 ° C," as pledged by the Paris Agreement.


Ocean warming and acidification (OWA), driven by unabated CO2 emissions, are expected to constrain the survival and reproduction of many marine organisms (1). Existing knowledge implies that physiological limits of early life history stages the vulnerability of species to OWA2). Studies of worst-case impact scenarios are important to raise the risk of awareness and gain social acceptance for mitigation policy (3). However, even more important is the identification of emissions pathways required to minimize impact risks and to locate potential refuge habitats of endangered species that should be prioritized in conservation (13). However, mechanism-based risk assessments that integrate vulnerable life stages and their specific habitat needs into a scenario context are barely available, especially for marine species inhabiting Arctic regions (4, 5).

The Subarctic and Arctic seas around Northern Europe (ie, Iceland Sea, Norwegian Sea, East Greenland Sea, and Barents Sea) are projected to experience higher rates of ocean warming, acidification, and sea-ice loss than most other marine areas on Earth (6). These ocean regions-previously termed the Seas of the North (7) – Are inhabited by highly productive fish populations, most of which undertake annual migration to specific spawning locations (4). The biophysical features of suitable spawning habitats support the survival of early life stages as well as their dispersal towards suitable nursery areas (8). Given that fish embryos are often more sensitive to environmental change than subsequent life stages (2), embryonic tolerance may act as a fundamental constraint on habitat habitat. For example, thermal tolerance ranges that are narrower in fish embryos than in other life stages may represent a biogeographic constraint (8) and are likely explained by incomplete development of cardiovascular and other homeostatic systems (9). Ocean acidification (OA) caused by elevated aquatic CO2 levels may exacerbate the disturbance of homeostasis (10), thereby narrowing the thermal range (2, 11) and possibly reducing spawning habitability by impairing egg survival.

Both Atlantic cod and Polar cod are key members of the Northern high-latitude fish fauna but differ in terms of thermal affinity and spawning preferences4, 5). Atlantic cod is a "thermal generalist" that occupies temperate to Arctic waters between -1.5 ° and 20 ° C (12). In contrast, Polar cod is a "thermal specialist", endemic to the High Arctic, and rarely found at temperatures above 3 ° C (13). Because of overlapping temperature ranges of juvenile and adult life stages, both species coexist during their summer feeding migrations (14). During winter and spring however, spawning occurs in separate locations with different water temperatures and sea-ice conditions (Figure 1). Given that Atlantic cod prefers warm waters (3 ° to 7 ° C) than Polar cod (-1 ° to 2 ° C), the latter species is considered to be particularly vulnerable to climate change5, 14). Moreover, another indirect threat to Polar cod reproduction is the projected loss of sea ice, which serves as a lounger childcare for larvae and juveniles during spring and summer (5).

FIG. 1 Distribution patterns of Atlantic cod and Polar cod in the Seas of the North.

(A) Atlantic cod; (B) Polar cod. Population of both species reproduces during winter and spring (Atlantic cod: March to May; Polar cod: December to March) at species-specific locations (ie spawning habitats, blue-shaded areas) with characteristic temperature and sea-ice conditions cod: 3 ° to 7 ° C, open water; Polar cod: -1 ° to 2 ° C, closed sea-ice cover). Green arrows indicate egg and larval dispersal driven by prevailing surface currents. During summer, the feeding grounds (green-shaded areas) of both species partly overlap, for example, around Svalbard, which marks the northernmost distribution limit of Atlantic cod. Red symbols indicate the origin of animals (spawning adults) used in this study. Distribution maps were redrawn after (4, 13, 33). NEW, Northeast Water Polynya; FJL, Franz Joseph Land; NZ, Novaya Zemlya.

The sponging aggregations of Atlantic and Polar cod-often comprising many million individuals-are important resources for humans and other marine predators. For example, the Norwegian Atlantic cod fishery alone generates an annual revenue of US $ 800 million (15), while Polar cod is an essential food item for many marine birds and mammals (5). Estimating changes in spawning habitability to these focal species therefore has high socioecological relevance (4). Functional responses of embryos to OWA incorporated into habitat models may help identify racial risks and benefits at varying emission scenarios, including the goal of limiting global warming to 1.5 ° C above preindustrial levels16).

Here, we evaluate embryonic ranges of thermal tolerance under OA in Atlantic cod and Polar cod. Oxygen consumption rates (MO2) or eyed-stage embryos and larval morphometrics at hatch provide insight into energetic constraints imposed by OWA. Spawning habitat suitability was mapped across the Seas of the North under different Representative Concentration Pathways (RCPs) by linking egg survival data with climate simulations of the Coupled Model Intercomparison Project Phase 5 (CMIP5). RCPs assume either "no greenhouse gas mitigation" (RCP8.5), "intermediate mitigation" (RCP4.5), or "strong mitigation" (RCP2.6). The latter scenario was developed with the goal of limiting the increase in global mean surface temperature (averaged over land and sea surface) to below 2 ° C relative to the reference period 1850-1900 and is suitable for providing a first estimate for the consequences of keeping global warming "well below 2 ° C, if not 1.5 ° C," as stated in the Paris Agreement (16).


Embryonic oxygen consumption (MO2) increased with increasing temperatures but dropped off or decreased at the warmest temperatures (Atlantic cod: ≥9 ° C; Polar cod: ≥4.5 ° C, Fig. 2, A and B), which, in combination with increased mortality under these conditions (Figure 3), indicative of severe heat stress. Embryos acclimated to lower temperatures (<9 ° / 4.5 ° C) and elevated Pco2 (partial pressure of CO2) consumed ~ 10% more oxygen compared to those reared under control Pco2. This trend was reversed after warming, indicating that additional oxygen and associated energy requirements under OA conditions can not be met at critical temperatures, causing the upper thermal limit of metabolic maintenance to decline. Higher energy requirements under elevated Pco2 may result from the cumulative costs of increased acid-base regulation, protein turnover, and damage repair (9, 10). The allocation of energy to life-sustaining functions should receive priority over growth (17th), as was evidenced by CO2– and warming-induced reductions in larval size at hatch (Fig. 2, C to F, and Fig. S2). The relative decrease in larval-free body area due to elevated Pco2 averaged 10% for Atlantic cod (P < 0.001) and 13% for Polar cod (P < 0.001), with the smallest larvae at the warmest temperature (Fig. 2, C and D, and Table S1). Reductions in larval body size and dry weight (Figs 2, E and F, and table S1) are in line with CO2-induced reallocation of energy away from growth also seen in other fish species18th).

FIG. 2 Effects of elevated Pco2 on temperature-dependent oxygen consumption rates (MO2) and growth of Atlantic cod embryos and Polar cod embryos (right).

(A and B) MO2 It was measured in eyed-stage embryos (image). Symbols are means (± SEM depicted as bars, n = 6 or 4). Performance curves (lines) are based on n = 28 data points. Dark and light shadings indicate 90 and 95% trusted confidence intervals, Bayesian. (C and D) Larval yolk-free body area at hatch was assessed as a indicator of somatic growth and resource (yolk) utilization. Box plots overlaid with individual values ​​show the 25th, 50th, and 75th percentile; Whiskers mark 95% confidence intervals. (D) Sufficient sample sizes were not available at 6 ° C because most individuals died or hatched malformed. (E and F) Offsets between regression lines (with 95% confidence intervals) indicate CO2-related differences in size-weight relationships of newly hatched larvae (image). Individuals were pooled across temperature treatments (E: 0 ° to 12 ° C, F: 0 ° to 3 ° C). (A to F) Significant main effects of temperature, Pco2, or their interaction (T * Pco2) are indicated by black ★, whereas orange ★ denotes significant CO2 effects of temperature treatments (tukey post hoc test, n = 6 or 4 per treatment). See table S1 for details on statistical tests. N.a., not available.

FIG. 3 Effects of elevated Pco2 on temperature-dependent egg survival in Atlantic cod and Polar cod.

(A) Atlantic cod; (B) Polar cod. Symbols represent means (± SEM depicted as bars, n = 6). Thermal performance curves (TPCs, lines) of each species are based on n = 36 data points. Dark and light shadings indicate 90 and 95% trusted confidence intervals, Bayesian. TPCs were extrapolated into subzero temperatures by incorporating freezing tolerance thresholds from the literature (Materials and Methods). Significant main effects of temperature, Pco2, or their interaction (T * Pco2) are indicated by black ★, whereas orange ★ denotes significant CO2 effects of temperature treatments (tukey post hoc test, n = 6 or 4 per treatment). See table S1 for details on statistical tests.

Egg survival decreased outside of preferred spawning temperatures of Atlantic cod (≤0 ° and ≥9 ° C) and polar cod (≥3 ° C), especially under the influence of elevated Pco2 (Figure 3 and Table S1). Accordingly, our results confirm that embryonic tolerance ranges represent a tight constraint on the thermal spawning niche of Atlantic cod and Polar cod. CO2Indirect mortality at their optimum spawning temperature was less pronounced for Atlantic cod (6 ° C, Figure 3A) than for Polar cod (0 ° to 1.5 ° C, Figure 3B). This observation corresponds with the variation in CO2 Sensitivity reported by previous studies on early-stage phases that tested for OWA effects solely under optimum temperature conditions (18th). However, both species experienced a similar CO2-related decline in egg survival at their respective warmer threshold (-48% at 9 ° C for Atlantic cod and -67% at 3 ° C for Polar cod). Increased thermal sensitivity of embryos under projected Pco2 levels implies a narrowing of their thermal tolerance range and thus the species reproductive niche (2). As a consequence, the spatial extent of thermally suitable spawning habitat for Atlantic cod and Polar cod may not only shift to higher latitudes in response to warming but also contract due to OWA.

Compared to contemporary (known) spawning sites of Atlantic cod and Polar cod in the study area (blue areas in Figure 1; yellow dashed areas in Figure 4), our baseline simulations (1985-2004) suggest that spawning occurs exclusively within the thermal optimum range of embryo development [>90% potential egg survival (PES), Fig. 4]. However, the area of ​​thermally suitable spawning habitat (PES> 90%) is larger than the area where spawning actually occurs. For example, despite suitable temperatures, no spawning of Atlantic cod is currently observed in the northeastern Barents Sea (19th), indicating that spawning habitat suitability also depends on factors other than temperature. Mechanisms that preclude certain areas as suitable for spawning may include aberrant dispersal of eggs and larvae, adverse feeding conditions, and predation pressure8, 19th).

FIG. 4 Current (baseline) spawning habitat suitability for Atlantic cod and Polar cod in the Seas of the North.

(A) Atlantic cod; (B) Polar cod. Spawning habitat suitability is expressed as PES (color code) by combining experimental survival data (Figure 3) with WOA13 temperature fields (1 ° × 1 °, upper 50 m of shelf seas) for the baseline period 1984-2005. Values ​​are averaged over spawning seasons (Atlantic cod: March to May; Polar cod: December to March) and referenced against locations where spawning has been documented[yellowdashedareas([yellowdashedareas(13, 33)]. The spatial extent of thermally suitable spawning habitat (PES> 90%) is typically larger than the "realized spawning habitat" because other limiting factors are not considered. Dotted magenta lines indicate the corresponding seasonal sea-ice edge positions (defined as areas with ice concentrations> 70%, note that sea-ice edge varies slightly between species due to varying species-specific spawning seasons).

By 2100, unabated OWA (RCP8.5) is projected to cause substantial decline in PES at major spawning sites of both species (Figure 5, A to C). For Atlantic cod, PES is projected to decrease Iceland (-10 to -40%) and the Faroe Islands (-20 to -60%) and along the entire Norwegian coast (-20 to -60%), including the most important spawning sites at the Lofoten archipelago (at 68 ° N, Figure 5A). In turn, extensive shelf regions off Svalbard and across the north-east Barents Sea will become more suitable (PES, +10 to + 60%) due to warming and decreasing sea-ice cover. However, potential gains in the North are constrained by reduced cold tolerance of Atlantic cod embryos under OA conditions and, possibly, unknown constraining factors (see above). Under RCP4.5, decreases in PES of Atlantic cod at some southern spawning sites (eg, Faroe Islands: -10 to -40%) are largely outweighed by thermal benefits (PES, +20 to + 60%) in the North Sea Barents Sea (between Svalbard, Franz Josef Land, and Novaya Zemlya, Fig. 5, D and F).

FIG. 5 Change in thermally suitable spawning habitat of Atlantic cod (left) and Polar cod (right) in the Seas of the North under RCPs.

(A to C) RCP8.5: Unabated OWA. (D to F) RCP4.5: Intermediate warming (no acidification considered). (G to I) RCP2.6: Less than 2 ° C global warming (no acidification considered). Maps show the shift in PES between the baseline period (1985-2004; spawning season of Atlantic cod: March to May; spawning season of Polar cod: December to March; see Figure 3) and the median of CMIP5 multimodel-based projections Seasonal sea surface temperature, 0 to 50 m; see Materials and Methods) for this century's end (2081-2100). The black shading indicates areas (cells, 1 ° × 1 °) with high uncertainty (ie, the shift in PES within that cell is smaller than the CMIP5 ensemble spread; see Materials and Methods). Dotted magenta lines represent the sea-ice edge positions of the respective species-specific spawning season (defined as areas with ice concentrations> 70%). (C, F, and I) For each map, values ​​(change in PES) of individual cells are summarized by estimates of kernel density, with the width corresponding to the relative occurrence of values. Box plots show the 25th, 50th, and 75th percentile; The ends of the whiskers mark the 95% intervals.

Polar cod will likely experience the most dramatic loss of spawning habitat south of Svalbard and Novaya Zemlya (PES, -40 to -80%; RCP8.5; Figure 5B). Moreover, Polar cod will lose its most under-ice habits except for a small refuge on the East Greenland shelf (Figure 5B). Even warming without OA effects (RCP4.5, Figure 5, E and F) will substantially reduce the suitability of important spawning habitats for Polar cod off Svalbard (PES, -20 to -60%) and Novaya Zemlya (PES, -10 to -40%). The widespread loss of sea ice under RCP8.5 and RCP4.5 scenarios may affect the reproductive success of Polar cod, because the ice protects spawning adults from predation and serves as a feeding habitat for early-life stages (5). Limiting global warming to about 1.5 ° C above preindustrial levels (ie, the average temperature of RCP2.6) may not only minimize reductions in PES at the current core spawning areas of both species to less than 10% (Figure 5, G to I) but also maintain some sea-ice cover.


Our projections suggest that OWA-driven impacts on egg survival and consequent changes in spawning habitability may be primary determinants of climate-dependent constraints on Atlantic cod and Polar cod. Present findings are in line with the hypothesis that tolerance of thermal ranges and embryonic habitats of both species are compressed by progressive OWA (2). Our results also corroborate the idea that unmitigated climate change represents an existential threat for cold-adapted species such as Polar cod (20), although we identified some cold refugia for this species in the High Arctic. Atlantic cod may follow the poleward displacement of its thermal optimum, possibly leading to the establishment of this commercially important species in regions currently dominated by Polar cod. The parallel decrease in the habitat suitability of Iceland and the Norwegian coast (under RCP8.5) implies, by 2100, spawning south of the Arctic Circle (e.g., south of the Lofoten) may no longer be possible for Atlantic cod. Potential displacement of commercially important fish stocks across management boundaries and exclusive economic zones poses major challenges not only to national fishermen and conservationists (5), but also to international bodies and regulations, which intend to avoid overexploitation, resource conflicts, and the degradation of pristine ecosystems in the Arctic (4, 21).

However, if global warming is limited to 1.5 ° C above preindustrial levels, changes in thermal suitability of present spawning habitats are unlikely to exceed critical thresholds of Atlantic cod and Polar cod. Residual risks may be reduced further as both species can potentially adapt to climatic changes, by responding either (i) via shifts in the timing and / or location of spawning within current regions (22) or (ii) through transgenerational processes that enhance physiological tolerance (23). Uncertainties in our results also relate to (iii) the reliability and resolution of the CMIP5 climate projections (24).

First, the temporal window for spawning in the North is limited to late winter-spring due to the extreme seasonality of light and associated primary production (food for planktonic larvae) at high latitudes (> 60 ° N) (22). Significant changes in spawning phenology are therefore unlikely to occur in this region. Instead, northward expansions of spawning during historic and ongoing warming periods are well documented, especially for Atlantic cod, which expanded its spawning activity to West Svalbard in the 1930s (25th). However, core spawning areas (eg, the Lofoten archipelago for the Barents Sea population) have always been occupied during past centuries, possibly due to favorable combinations of biotic and abiotic factors that maximize recruitment success (8, 22). After spraying, dispersal of eggs and larvae to suitable nursery areas – sometimes over hundreds of kilometers-plays is a major role in terms of life-cycle connectivity and population replenishment (8). Spawning at alternative locales (as required under RCP8.5 for both species and under RCP4.5 for Polar cod) could disturb connectivity and thus increase the risk of advective losses and recruitment failure8). Accordingly, successful establishment of new spawning habits will largely depend on a number of factors in addition to egg survival (i.e., prey availability, predation pressure, and connectivity), all of which are currently difficult to predict (2, 22).

Secondly, our results assume that embryonic tolerance ranges are constant across different populations and generations (ie, no evolutionary change within this century). These assumptions are supported by experimental data[egsimilartemperatureoptimaforeggdevelopmentamongdifferentAtlanticcodpopulations([egsimilartemperatureoptimaforeggdevelopmentamongdifferentAtlanticcodpopulations(26th); see also fig. S1], as well as by field observations[egconsistentnorthwardshiftofcodspawningactivityinresponsetoprevious/ongoingwarming([egconsistentnorthwardshiftofcodspawningactivityinresponsetoprevious/ongoingwarming(17th)]and phylogenetic analyzes of thermal tolerance evolution in marine fish[eg<01°Cchangeinthermaltoleranceper1millionyears([eg<01°Cchangeinthermaltoleranceper1millionyears(27th)]. Transgenerational plastics (TGP) may promote short-term adaptation to environmental change via nongenetic inheritance (eg, maternal transmission) (23). However, in contrast to the theory of TGP, experiments on Atlantic cod suggest that egg viability is impaired during similar degrees of warming if the female are exposed during gonad maturation28). This example of negative TGP corresponds to the majority (57%) of studies on TGP in fish that observed either neutral (33%) or negative (24%) responses (29). Given the limited capacity for short-term adaptation, it is most likely that species have to abandon their traditional habitats as soon as physiological limits are exceeded2). Accordingly, our results identify not only high-risk areas, but also potential refuge habitats that should be prioritized in respect of the implementation of marine reserves.

Third, CMIP5 climate projections include uncertainties (24). To some degree, these uncertainties can be reduced and assessed by considering multimodel results (see Materials and Methods). Near-coastal habitats are poorly represented in current global climate models (24). The confidence of climate impact projections for these areas could be improved in future studies, most elegantly by means of global multiresolution ocean models with unstructured meshes (30th).

In light of embryonic intolerance to OWA, we show that with unabated greenhouse gas emissions, large areas presently used for spawning will become less suitable for recruiting Atlantic cod and Polar cod, possibly leading to cascading effects on Arctic food webs and associated ecosystem services4, 5). However, our results also emphasize that migration measures, as pledged by the Paris Agreement, can ameliorate climate change effects on both species. Given that current CO2 emissions trajectories yield at 1% chance of limiting global warming to 1.5 ° C above preindustrial levels (31), our results call for immediate emission cuts following scenarios compatible with warming at 1.5 ° C to prevent irreversible ecosystem damage in the Arctic and elsewhere.



The Atlantic cod was caught by longlining in the southern Barents Sea in March 2014. Mature fish were transported to the Center for Marine Aquaculture (Nofima AS, Tromsø, Norway) and held in a flow-through tank (25 m3) under ambient light, salinity [34 practical salinity units (PSU)], and temperature conditions (5 ° ± 0.5 ° C). Polar cod was captured in Kongsfjorden (West Svalbard: 78 ° 95'02 "N, 11 ° 99'84" E) by trawling in January 2014. Selected fish were held in flow-through tanks (0.5 m3) and transferred to the Aquaculture Research Station in Karvikå (NOFIMA, The Arctic University of Norway UiT, Tromsø). At the station, the fish were kept in a flow-through tank (2 m3) at 3 ° ± 0.3 ° C water temperature (34 PSU) and complete darkness. In both experiments, gametes used for in vitro fertilization were obtained by strip spawning from n = 13 (Polar cod: 12) males and n = 6 female (table S2).

Fertilization protocol

All fertilizers were conducted within 30 minutes after stripping. Each egg batch was split into half and fertilized using filtered and ultraviolet (UV) sterilized seawater (34 PSU) previously adjusted to the broodstock holding temperature (Atlantic cod: 5 ° C; polar cod: 3 ° C) and two different Pco2 conditions[control[controlPco2: 400 μm, pH(Free Scale) 8.15; high Pco2: 1100 μm, pHF 7.77]. A standardized dry fertilization protocol with milt aliquots from n = 3 men used to maximize fertilization success (32).

Fertilization success

Fertilization success was assessed in subsamples (3 × 100 eggs per batch and Pco2 treatment), which were incubated within sealed petri dishes until the 8/16-cell stage (Atlantic cod: 12 hours, 5 ° C, Polar cod: 24 hours, 3 ° C) and photographed under a stereomicroscope for subsequent evaluation (table S3 ). These images were also used to determine the mean egg diameter of an egg batch (30 eggs per batch, table S3).

Incubation setup

According to different spawning seasons, both experiments could be conducted sequentially with the same experimental setup in 2014 (Polar cod: February to April; Atlantic cod: April to May). Eggs previously fertilized at either control or high Pco2 were maintained at the respective CO2 Treatment and incubated until swallowing at five different temperatures (Atlantic cod: 0 °, 3 °, 6 °, 9 °, and 12 ° C; Polar cod: 0 °, 1.5 °, 3 °, 4.5 °, and 6 ° C) . Temperature range was selected to cover spawning preferences of Atlantic cod (3 ° to 7 ° C) (33) and Polar cod (≤2 ° C) (13) and projected warming scenarios for the respective region. Each treatment group of an egg batch was subdivided into two stagnant incubators (20 incubators per female, 120 in each experiment). To not bias survival estimates, only one of the two incubators was used to evaluate egg survival (and larval morphometrics at hatch), while subsamples required for embryonic MO2 Measurements were taken from the second incubator.

Initially, all incubators (volume, 1000 ml) were filled with filtered (0.2 μm) and UV-sterilized seawater (34 PSU) adjusted to the respective fertilization treatment and stocked with positively buoyant eggs. With regard to oxygen supply in a stagnant incubator, it is important to ensure that the eggs have enough space to arrange themselves in a single layer under the water surface. We therefore adjusted the amount of eggs per incubator (Atlantic cod: ~ 300 to 500; Polar cod: ~ 200 to 300) according to differences in egg size between Atlantic cod (~ 1.45 mm) and Polar cod (~ 1.65 mm). Loaded incubators were then located in differently thermostated seawater baths (volume, 400 liters) to ensure a smooth temperature change inside the incubator. The transparent, bottom-tapered incubators were sealed with a Styrofoam cover to prevent CO2 outgassing and temperature fluctuations. According to natural light regimes, Atlantic cod eggs received dim light with a daily rhythm of 8 hours light / 16 hours darkness, and Polar cod eggs were kept in darkness except for dim light exposure during handling. Every 24 hours, 90% of the water volume of each incubator was replaced by filtered (0.2 μm) and UV-sterilized seawater to prevent oxygen depletion. An outlet valve was mounted at the bottom of the incubators to drain the seawater with dead eggs, which lost buoyancy and down to the bottom. Each seawater bath contained two 60-liter reservoir tanks, which were used to pre-seal seawater to the corresponding temperature and Pco2 conditions. Water temperatures inside the water baths were controlled by thermostats and recorded every 15 min (± 0.1 ° C) via a multichannel aquarium computer (IKS Aquastar, IKS Systems, Germany). Future Pco2 Conditions were established by injection of pure CO2 Gas into the submerged 60-liter reservoir tanks at each temperature. A multi-channel feedback system (IKS-Aquastar), connected to individual pH probes (IKS-Aquastar) and solenoid valves, was used to control pH water and Pco2 values. The Pco2 or the reservoir tanks were measured in situ before each water exchange with an infrared Pco2 probe (Vaisala GMP 343, manual temperature compensation, ± 5 μatm accuracy; Vaisala, Finland). The probe was equipped with a MI70 Reading device and an aspiration pump, which was connected to a degassing membrane (G541, Liqui-Cel, 3M, USA) to measure Pco2 in air equilibrated to dissolved water gases (34). Factory calibration was confirmed by seawater measurements previously bubbled with a technical gas mixture (1000 μm CO2 in air, Air Liquide, Germany). Before the daily water exchange, pH values ​​of the reservoir tanks were measured with a pH electrode to three decimal places (Mettler Toledo InLab Routine Pt 1000 with temperature compensation, Mettler Toledo, Switzerland), which was connected to a WTW 3310 pH meter. A two-point calibration with NBS (National Bureau of Standards) buffers was performed on a daily basis. To convert NBS to the free proton concentration scale for seawater pH (35), the electrode was calibrated with tris-HCl seawater buffer (36), which were acclimated to the corresponding incubation temperature before each measurement. Seawater pH values ​​refer to the free pH scale (pHF) throughout this manuscript. Seawater parameters are summarized in fig. S3.

Egg survival

Egg mortality was recorded on a 24-hour basis until all individuals within a incubator had either died or hatched (fig. Once hatching commenced, free-swollen larvae were collected in the morning, euthanized with a overdose of tricaine methanesulfonate (MS-222), and counted after visual examination for morphological deformities under a stereomicroscope. The incidence of larval deformities was quantified as the percentage of hatchings exhibiting severe deformations of the yolk sac, cranium, or vertebral column. Egg survival was defined as the percentage of non-aligned, viable larvae that hadched from the initial number of fertilized eggs (fig. S5). The proportion of fertilized eggs within a incubator was estimated from the mean fertilization success of the respective egg batch (table S3).


Oxygen consumption rates (MO2) or eyed-stage embryos (at 50% eye pigmentation, fig. S4) were measured in closed, temperature-controlled respiration chambers (OXY0 41 A, Collotec Meßtechnik GmbH, Germany). The double-walled chambers were connected to a flow-through thermostat to adjust the temperature of the respiration chamber to the corresponding incubation temperature of the eggs. Measurements were conducted in triplicate with 10 to 20 eggs of each female and treatment combination. Eggs were placed in the chamber with a volume of 1 ml of sterilized seawater adjusted to the corresponding Pco2 treatment. A magnetic microstar (3 mm) was placed under the floating eggs to prevent oxygen stratification within the respiration chamber. The change in oxygen saturation was detected by micro-optodes (fiber-optic microsensor, flat broken tip, diameter: 140 μm, PreSens GmbH, Germany) connected to a Microx TX3 (PreSens GmbH, Germany). Recordings were stopped as soon as the oxygen saturation declined below 80% air saturation. Subsequently, the water volume of the respiration chamber and wet weight of the measured eggs (gww) were determined by weighing (±1 mg). Oxygen consumption was expressed as[nmolO[nmolO2 (gww * min)−1]and corrected for bacterial oxygen consumption (<5%) and optode drift, which was determined by blank measurements before and after three successive egg respiration measurements.

Larval morphometrics

Subsamples of 10 to 30 nonmalformed larvae from each female and treatment combination were photographed for subsequent measurements of larval morphometrics (standard length, yolk-free body area, total body area, and yolk sac area) using Olympus image analysis software (Stream Essentials, Olympus, Tokyo, Japan). Only samples obtained from the same daily cohort (during peak hatch at each temperature treatment) were used for statistical comparison. After being photographed, 10 to 20 larvae were freeze dried to determine individual dry weights (±0.1 μg, XP6U Micro Comparator, Mettler Toledo, Columbus, OH, USA). Replicates with less than 10 nonmalformed larvae were precluded from statistical analyses.

Statistical analysis

Statistics were conducted with the open source software R, version 3.3.3 ( Linear mixed effect models[package“lme4”([package“lme4”(37)]were used to analyze data on egg survival and MO2. In each case, we treated different levels of temperature and Pco2 as fixed factors and included “female” (egg batch) as a random effect. Differences in larval morphometrics (yolk-free body area, total body area, dry weight, standard length, and yolk sac area) were determined by multifactorial analysis of covariance. These models were run with temperature and Pco2 as fixed factors and egg diameter as a covariate. Levene’s and Shapiro-Wilk methods confirmed normality and homoscedasticity, respectively. The package “lsmeans” (38) was used for pairwise comparisons (P values were adjusted according to Tukey’s post hoc test method). All data are presented as means (± SEM) and statistical tests with P < 0.05 were considered significant. Results are summarized in table S1.

Curve fitting

Generalized additive models[package“mgcv”([package“mgcv”(39)]were used to fit temperature-dependent curves of successful development building on egg survival and MO2. This method has the benefit of avoiding a priori assumptions about the shape of the performance curve, which is crucial in assessing the impact of elevated Pco2 on thermal sensitivity. “Betar” and “Gaussian” error distributions were used for egg survival and MO2 data, respectively. To avoid overfitting, the complexity of the curve (i.e., the number of degrees of freedom) was determined by penalized regression splines and generalized cross-validation (39). Models of egg survival were constrained at thermal minima because eggs of cold-water fish can survive subzero temperatures far below any applicable in rearing practice. Following Niehaus et al. (40), we forced each model with artificial zero values (n = 6) based on absolute cold limits from the literature. These limits were set to −4°C for Atlantic cod (41) and −9°C for Polar cod assuming similar freezing resistance, as reported for another ice-associated fish species from Antarctica (42).

Spawning habitat maps

Fitted treatment effects on normalized egg survival data (fig. S6A; raw data are shown in Fig. 3) were linked to climate projections for the Seas of Norden to infer spatially explicit changes in the maximum PES under different RCPs. That is, the treatment fits were evaluated for gridded upper-ocean water temperatures (monthly averages) bilinearly interpolated to a horizontal resolution of 1° × 1° and a vertical resolution of 10 m. To account for species-specific reproduction behavior, we first constrained each map according to spawning seasonality and depth preferences reported for Atlantic cod[MarchtoMay50to400m([MarchtoMay50to400m(33)]and Polar cod[DecembertoMarch5to400m([DecembertoMarch5to400m(13)]. As both species produce pelagic eggs that immediately ascend into the upper mixed layer if spawned at greater depths (13, 33), we further limited the eligible depth range to the upper 50 m. PES at a given latitude and longitude was then estimated from the calculations by selecting the value at the depth of maximum egg survival (at 0 to 50 m depth). Egg dispersal was not considered since the major bulk of temperature- and acidification-related mortality occurs during the first week of development (fig. S4).

Oceanic conditions were expressed as climatological averages of water temperatures, sea-ice concentrations, and the pH of surface water. Our observational baseline is represented by monthly water temperatures[WOA13([WOA13(43)]and sea-ice concentrations[HadISST([HadISST(44)], averaged from 1985 to 2004, and by pH values averaged over the period 1972–2013[GLODAPv2([GLODAPv2(45, 46)]. Simulated ocean climate conditions were expressed as 20-year averages of monthly seawater temperatures and sea-ice concentrations and of 20-year averages of annual pH values of surface water. End-of-century projections were derived from climate simulations for 2081–2100 carried out in CMIP5 (45). We considered only those 10 ensemble members (see table S4) that provide data on each of the relevant parameters (water temperature, sea ice, and pH) under RCP8.5, RCP4.5, and RCP2.6 (47). Projected pH values and temperatures are shown in fig. S6 (E to L). To account for potential model biases, we diagnosed for each of the 10 CMIP5 models the differences between simulations and observations for the baseline period and subtracted these anomalies from the CMIP5-RCP results for 2081–2100. For 2081–2100, we considered the CMIP5-RCPs ensemble median of maximum PES and assessed the uncertainty of PES at a given location by defining a signal-to-noise ratio that relates the temporal change in PES between 2081–2100 and 1985–2004 (ΔPES) to the median absolute deviation (MAD) of results for 2081–2100. Model results are not robust where the temporal change in PES is smaller than the ensemble spread, i.e., ΔPES/MAD < 1. PES calculations for scenarios RCP2.6 and RCP4.5 were carried out for Pco2 = 400 μatm. The effect of elevated Pco2 (1100 μatm) on PES was only considered under scenario RCP8.5.


Supplementary material for this article is available at

Fig. S1 Thermal niches of adult Atlantic cod and Polar cod.

Fig. S2 Treatment effects on larval morphometrics at hatch.

Fig. S3. Water quality measurements.

Fig. S4. Effects of temperature and Pco2 on daily mortality rates of Atlantic cod and Polar cod.

Fig. S5. Effects of temperature and Pco2 on embryonic development of Atlantic cod and Polar cod.

Fig. S6. Spawning habitat maps for Atlantic cod and Polar cod are based on experimental egg survival data and climate projections under different emission scenarios.

Table S1. Summary table for statistical analyses conducted on data presented in Figs. 2 and 3 of the main text and in figs. S1 and S5.

Table S2. Length and weight of female and male Atlantic cod and Polar cod used for strip spawning and artificial fertilization.

Table S3. Mean egg diameter and fertilization success of egg batches (±SD, n = 3) produced by different females (n = 6).

Table S4. List of CMIP5 models that met the requirements for this study (for details, see the “Spawning habitat maps” section in the main text).

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Acknowledgments: We acknowledge the support of S. Hardenberg, E. Leo, M. Stiasny, C. Clemmensen, G. Göttler, F. Mark, and C. Bridges. Special thanks are dedicated to the staff of the Tromsø Aquaculture Research Station and the Centre for Marine Aquaculture. Funding: Funding was received from the research program BIOACID [Biological Impacts of Ocean Acidification by the German Federal Ministry of Education and Research (BMBF), FKZ 03F0655B to H.-O.P. and FKZ 03F0728B to D.S.]. Funding was also received from AQUAculture infrastructures for EXCELlence in European fish research (AQUAEXCEL, TNA 0092/06/08/21 to D.S.). F.T.D., M.B., H.-O.P., and D.S. were supported by the PACES (Polar Regions and Coasts in a Changing Earth System) program of the Alfred Wegener Institute, Helmholtz Centre for Polar and Marine Research (AWI). Previous and additional support from grants POLARIZATION (Norwegian Research Council grant no. 214184 to J.N.) and METAFISCH (BMBF grant no. FZK01LS1604A to H.-O.P. and F.T.D.) are also acknowledged. Author contributions: F.T.D. and D.S. devised the study and designed the experiments. F.T.D. conducted the experiments. J.N., V.P., and A.M. provided equipment and facility infrastructure. F.T.D. analyzed the experimental data. M.B. analyzed climate data and generated habitat maps. F.T.D. drafted the manuscript. F.T.D., D.S., M.B., and H.-O.P. wrote the manuscript. J.N., V.P., and A.M. edited the manuscript. Competing interests: The authors declare that they have no competing interests. Data and materials availability: All data needed to evaluate the conclusions in the paper are present in the paper and/or the Supplementary Materials. Additional data related to this paper may be requested from the authors. The experimental data supporting the findings of this study are available from PANGEA (, a member of the ICSU World Data System.

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