Introduction
Climate change is widely recognized as the greatest threat to the diversity, stability and functioning of the world’s marine ecosystems (Brierley and Kingsford, Reference Brierley and Kingsford2009; Hoegh-Guldberg and Bruno, Reference Hoegh-Guldberg and Bruno2010; Doney et al., Reference Doney, Ruckelshaus, Emmett Duffy, Barry, Chan, English, Galindo, Grebmeier, Hollowed, Knowlton, Polovina, Rabalais, Sydeman and Talley2012). Seabirds are among the many organisms likely to be severely impacted by climate change (Dias et al., Reference Dias, Martin, Pearmain, Burfield, Small, Phillips, Yates, Lascelles, Borboroglu and Croxall2019). They play key roles in marine ecosystems, from nutrient transfer to habitat connectivity (Signa et al., Reference Signa, Mazzola and Vizzini2021), and they are widely seen as indicators of ecosystem health (Piatt and Sydeman, Reference Piatt and Sydeman2007; Parsons et al., Reference Parsons, Mitchell, Butler, Ratcliffe, Frederiksen, Foster and Reid2008). A recent overview of the impact of heatwaves (and global warming in general) on seabirds covers several mechanisms ranging from habitat modification to physiological stress (Piatt et al., Reference Piatt, Arimitsu, Thompson, Suryan, Wilson, Elliott and Sydeman2024). Surprisingly, there is not a single mention in this review of the possible impact of rising sea temperatures on the dynamics, severity and geographic distribution of parasites and diseases affecting seabirds. This is a glaring omission, as global warming has been widely recognized for over two decades as a key driver of current and future changes in parasite infections across marine habitats (Marcogliese, Reference Marcogliese2001; Harvell et al., Reference Harvell, Mitchell, Ward, Altizer, Dobson, Ostfeld and Samuel2002; Poulin and Mouritsen, Reference Poulin and Mouritsen2006; Burge et al., Reference Burge, Mark Eakin, Friedman, Froelich, Hershberger, Hofmann, Petes, Prager, Weil, Willis, Ford and Harvell2014; Byers, Reference Byers2020).
In coastal ecosystems where the life cycles of helminth parasites have been well resolved, such as that of southern New Zealand (Bennett et al., Reference Bennett, Presswell and Poulin2023), seabirds have been shown to play key roles as definitive hosts. Among marine parasites, including those infecting seabirds, that are most likely to be impacted by global warming, trematodes stand out. Several stages of their life cycle are notoriously sensitive to temperature. In particular, small changes in water temperature can have huge effects on the rate at which infective stages, i.e. cercariae, are produced within and released from molluscan first intermediate host (Poulin, Reference Poulin2006; Selbach and Poulin, Reference Selbach and Poulin2020) as well as their survival and infectivity to the second intermediate host (Koprivnikar, Reference Koprivnikar2010; Morley and Lewis, Reference Morley and Lewis2015). These temperature-driven effects on trematode biology can have drastic consequences on host populations (Mouritsen and Jensen, Reference Mouritsen and Jensen1997; Mouritsen et al., Reference Mouritsen, Tompkins and Poulin2005) and communities (Mouritsen et al., Reference Mouritsen, Sørensen, Poulin and Fredensborg2018). Although these impacts are often documented for invertebrate intermediate hosts, there is no reason they cannot extend to vertebrates as well.
The present study investigates the seasonal response of an unusual trematode, Copiatestes thyrsitae Cowcroft, 1948, to changes in its thermal environment, and the potentially serious consequences of any rise in its abundance for seabirds. Copiatestes spp. (Family Syncoelidae) are relatively little known, enigmatic parasites with atypical life cycles and large impacts on their surrounding communities. Presumably, they follow a three-host life cycle (Gibson and Bray, Reference Gibson and Bray1977), including a molluscan first intermediate host (although none have been discovered yet), a euphausiid second intermediate host (Morales-Ávila et al., Reference Morales-Ávila, Gómez-Gutiérrez, Gómez Del Prado-Rosas and Robinson2015; Bennett et al., Reference Bennett, Presswell and Poulin2023) and a fish definitive host (Manter, Reference Manter1954; Gibson and Bray, Reference Gibson and Bray1977; Bennett et al., Reference Bennett, Presswell and Poulin2023) (Figure 1). While most other trematode taxa have only two free-living stages, the miracidium stage that seeks out the first intermediate host, and the cercaria stage, between first and second intermediate hosts (Poulin, Reference Poulin2007), Copiatestes spp. have an additional one between the second and definitive hosts, as noted by several authors (Odhner, Reference Odhner1911; Dollfus, Reference Dollfus1966; Claugher, Reference Claugher1976; Bennett et al., Reference Bennett, Presswell and Poulin2023) (Figure 1). Within this stage, individuals possess a pair of bladder-like bodies and byssus-like filaments extending from the terminal tip of the body (Gibson, Reference Gibson1976). The purpose of this additional life stage and morphological structures remains elusive, although Claugher (Reference Claugher1976) hypothesized that diurnal migrations of euphausiids may have promoted Copiatestes spp. to evolve the use of a third free-living stage, with the sticky filaments likely increasing the probability of coming into physical contact with their fish definitive hosts (Claugher, Reference Claugher1976). The existence of this additional stage has ecological consequences for marine life, as non-target organisms can become entangled in Copiatestes’ sticky filaments (e.g. Claugher (Reference Claugher1976).
Figure 1. Schematic illustrating the presumed life cycle of Copiatestes thyrsitae. The second intermediate host and subsequent free-living stage are the focus of this study.
Reports of Copiatestes entanglement with seabird tarsi highlight their ecological importance. These entanglements, often referred to as ‘seabird anklets’, have been documented in various species of petrels and prions (Family Procellariidae), particularly around off-shore islands in the South Atlantic, Antarctic and South Pacific (Claugher, Reference Claugher1976; Furness, Reference Furness1984; Imber, Reference Imber1984; Ryan, Reference Ryan1986). Of the few times this association has been documented in the literature, impacts on seabird movement, is often negligible. However, one record exists of Copiatestes being associated with the mass mortality of an estimated over 200 000 seabirds in the Chatham Islands in the 1970s (Claugher, Reference Claugher1976). Birds presumably starved because they were unable to take off from land after being entangled with anklets while feeding at sea. Six bird species were involved in that event; since then, and not during any mortality event, Imber (Reference Imber1984) reported anklets present (but not limiting tarsi movement) on three of these native petrels and prions. A large-scale survey off the coast of South Africa also revealed that anklets are associated with smaller bodied species and those with a diet including euphausiids (Imber, Reference Imber1984).
Here, we present the results of a 12-month monitoring program that aimed to assess the occurrence of Copiatestes thyrsitae in its second intermediate host, Nyctiphanes australis G. O. Sars, 1883 (hereafter referred to as euphausiid) and that of its third free-living stages in Otago Harbour, South Island, New Zealand. We specifically test the causal role of sea temperature in driving temporal changes in the abundance of this parasite, and thus in the risks of entanglement for seabirds. Our findings reveal how the abundance of this parasite peaks at higher temperatures, and that it is nonetheless present throughout the year in both its second intermediate host and as free-living stages. Finally, we comment on the bird species at highest risk of Copiatestes entanglement during any future heatwave events.
Materials and methods
This study was conducted between September 2023 and August 2024 at the New Zealand Marine Studies Centre, University of Otago in Dunedin, New Zealand. Approximately every 2 weeks, one 250-micron (48 cm diameter) plankton net was deployed at the end of the centre’s wharf (approximate GPS coordinates: latitude −45.827925, longitude 170.639939) and left overnight for at least 16 h. Owing to the hydrology of the Otago Harbour, there can be two distinct biodiversity signals depending on whether sampling occurs in the upper or lower harbour (one being benthic and the other oceanic). The sample location is placed advantageously in that it receives both outgoing tidal water and incoming coastal water bodies with each tidal cycle allowing for representation of species from both. Each plankton sample was either processed immediately after collection, or kept in a 30 L bucket with an air bubbler for a few hours until processing. This was to reduce the possibility of euphausiid death and incorrect identification of free-living stages of C. thyrsitae that would emerge after host death. In each sample, the following was recorded: the total number of second intermediate hosts of C. thyrsitae (euphausiid N. australis), whether each euphausiid was infected (Figure 2a) and if so by how many C. thyrsitae, and the number of C. thyrsitae in their third free-living stage (Figure 2b). Infections and the free-living stage was identified with the use of a dissecting microscope whereby the whole plankton sample was screened and life stages identified (see Figure 2b for example of third free-living stage). The third free-living stage was counted if a Copiatestes individual was in plankton sample, but not infecting a host. If a deceased krill host was in the sample with a broken carapace (meaning it is feasible that the Copiatestes had just emerged because their host had died) then this was not counted as free-living. We also measured the body length of a subsample of infected and uninfected euphausiids under a dissecting microscope: total body length was measured from the tip of the rostrum to the end of the tail fan.
Figure 2. Photo micrographs of (a) euphausiid (Nyctiphanes australis) infected with Copiatestes thyrsitae, (b) C. thyrsitae third free-living stage, attached to surrounding material, (c) numerous Copiatestes individuals and filaments removed from a bird tarsus, and, (d) a close up of C. thyrsitae individuals entangled from a bird tarsus. Scale a–b, d = 2 mm, c = 2.5 cm.
For each plankton collection, we calculated various parasite descriptors following Bush et al. (Reference Bush, Lafferty, Lotz and Shostak1997). These included prevalence defined as the percent of hosts infected with C. thyrsitae within each sample, mean intensity defined as the average number of C. thyrsitae individuals per infected euphausiid host, and mean abundance defined as the average number of C. thyrsitae individuals per euphausiid host (including infected and uninfected ones). Sea surface temperature at the location of collection was recorded as a single daily reading by Portobello Marine Laboratory as part of an existing long-term time series of single daily recordings (Shears and Bowen, Reference Shears and Bowen2017).
For a graphical representation of temporal changes in prevalence over the study duration, we plotted prevalence with Clopper–Pearson 95% confidence intervals for each sample, the number of free-living stages recovered per sample, and the sea surface temperature at the time of sampling.
All data analyses and visualizations were conducted in R (R Core Team, 2023) using packages stats (R Core Team, 2023) and ggplot2 (Wickham et al., Reference Wickham, Chang, Henry, Pedersen, Takahashi, Wilke, Woo, Yutani, Dunnington and van den Brand2025). Generalized linear models (GLMs) were used to test the influence of temperature on parasite parameters (including prevalence, mean abundance, mean intensity and number of free-living stage individuals found as response variables) with function glm(). The data for all parasite descriptors was non-normal (quantified with Shapiro–Wilk tests [Shapiro and Wilk, Reference Shapiro and Wilk1965]) and all but number of free-living stage individuals were over-dispersed (dispersal values greater than 1 [Gelman and Hill, Reference Gelman and Hill2006]). Therefore, distribution and link functions for the GLMs were allocated as follows: prevalence = quasi-binomial with logit function, mean abundance and mean intensity = quasi-poisson with log function and number of free-living stage individuals (count data) = poisson with log function. For each GLM, various temperature profiles were used as our explanatory variables to account for any potential time lag between peaks in temperature and increased shedding of cercariae by the unknown first intermediate host, resulting in euphausiid infections. These temperature profiles were as follows: Day 0 (temperature on the day of plankton collection), Week 1 (average temperature for the 0–7 days preceding sampling), Week 2 (average temperature for the 8–14 days preceding sampling), Week 3 (average temperature for the 15–21 days preceding sampling), Month 1 (average temperature for the 0–30 days preceding sampling), Month 2 (average temperature for the 31–60 days preceding sampling), Month 3 (average temperature for the 61–90 days preceding sampling), and Max Month 1 (maximum sea surface temperature observed during the month prior to sampling). We used deviance explained (a measure of model fit – the proportion of variance in response variable accounted for by the model) to determine which time lag provided the best fit for each parasite parameter. To account for testing multiple comparisons and increased risk of Type 1 error, we applied a Bonferroni correction to our resulting p-values (Haynes, Reference Haynes, Dubitzky, Wolkenhauer, Cho and Yokota2013).
Finally, to determine whether infected euphausiids had smaller body lengths on average than uninfected individuals, we compared the two groups with a Mann–Whitney test.
Results
A total of 3954 euphausiids were collected from Otago Harbour between September 2023 and August 2024 (Table 1). Of these, 237 individuals were infected with Copiatestes thyrsitae, harbouring a total of 303 parasites, with an overall prevalence of 5.9% across all sampling dates. The number of hosts collected per sample ranged from 1 to 973, with an average of 146 euphausiids per sample. The prevalence of C. thyrsitae ranged from 0 to 100% (average prevalence = 13.5%). Most infections involved just one C. thyrsitae individual per host, although the largest sample (n = 973) included several multiple infections (34 double, 1 triple, and 1 quadruple). We recovered 26 free-living stages of C. thyrsitae from the water column within plankton nets during our collections. These free-living stages were found in about 40% of sampling dates. Overall, prevalence, mean abundance, intensity, number of free-living stages recovered, and sea surface temperature varied substantially across the sampling period of this study (Table 1; Figure 3).
Figure 3. Prevalence of infection with Clopper–Pearson 95% confidence intervals, number of free-living stage individuals recovered from plankton net, and daily sea surface temperature per plankton sampling event of Copiatestes in euphausiid (Nyctiphanes australis) at Otago Harbour, New Zealand between September 2023 and August 2024. See Table 1 for sample sizes.
Table 1. Parasite data from plankton nets deployed repeatedly in Otago Harbour, Dunedin, New Zealand between September 2023 and August 2024, including number (N) of euphausiids (N. australis) obtained, number infected with Copiatestes thyrsitae, number of free-living C. thyrsitae individuals obtained, prevalence, mean abundance, and mean intensity for infected euphausiids
Significant correlations were observed between parasite infection parameters and temperature across time periods prior to host collection (Table 2; Figure 4). Strong significant positive relationships were observed between mean abundance and prevalence, and sea surface temperature (Table 2). As temperature increased, abundance of C. thyrsitae within infected hosts and percentage of infected hosts increased (Table 2; Figure 4). This relationship was observed for temperature combinations of up to 1 month prior to collection of the hosts, including temperature on the collection day (Day 0), the average temperature of 1 (Week 1), 2 (Week 2), and 3 (Week 3) weeks prior to collection, average temperature for 1 month prior (Month 1), and the highest maximum temperature observed for 1 month prior to collection (Max Month 1) (Table 2). The strength and significance of these positive correlations were relatively consistent across time profiles (deviance explained ranged 32–64% and p-values ≤ 0.05). The average temperature 2 weeks prior to sampling (Week 2) explained the highest deviance compared to other time profiles for predicting mean abundance and prevalence (deviance explained = 64% and 59%, respectively). The coefficient estimates suggested that with every 1 °C increase in the average temperature 2 weeks prior to sampling, the log-odds of prevalence and abundance increase is 0.24 and 0.25, respectively. No infection parameter (prevalence, mean abundance, mean intensity, number of free-living stages) was significantly correlated with the average temperature of the sea surface 2 or 3 months prior to collection of hosts (Month 2 and Month 3; Table 2), except for prevalence at Month 2 which was slightly significant (p = 0.01) with moderate fit (Table 2). We found no effect of sea surface temperature and the number on free-living individuals and mean intensity for any of the time profiles tested (Table 2).
Figure 4. Relationships between temperature and (a) mean abundance and (b) prevalence (%) of Copiatestes infecting euphausiids (Nyctiphanes australis) in Otago, New Zealand. Each panel displays the relationship between different temperature profiles (Day 0, Max Month 1, Week 1, Week 2, Week 3, Month 1, Month 2 and Month 3) and parasite parameter based on generalized linear models. Lines represent statistically significant relationships, and shaded areas denote 95% confidence intervals.
Table 2. Generalized linear models exploring relationships between parasite descriptors (prevalence, mean abundance, mean intensity and number (n) of free-living individuals) and sea surface temperature taken over different time periods prior to sampling, including: temperature of water on collection day (Day 0), average temperature of 1, 2, and 3 weeks and months prior to collection (Week 1, Week 2, Week 3, Month 1, Month 2, Month 3), and the maximum temperature of the previous month (Max Month 1). P-values reported as uncorrected and Bonferroni corrected in brackets. SE denotes standard error. Statistically significant results are bolded
We found a statistically significant difference between the average total length of infected euphausiids and that of uninfected euphausiids (p = 0.019, w = 354.5; Figure 5). The median size of uninfected euphausiids was 7.14% greater than infected euphausiids (median size: uninfected = 14 mm, infected = 15 mm).
Figure 5. Average size (mm) of euphausiid (Nyctiphanes australis) uninfected and infected by Copiatestes thyrsitae in Otago Harbour, New Zealand. N uninfected = 100, N infected = 11. Error bars represent 95% confidence intervals.
Discussion
Rising sea temperatures resulting from global warming are predicted to interact with parasitism to impact marine life (Marcogliese, Reference Marcogliese2001; Harvell et al., Reference Harvell, Mitchell, Ward, Altizer, Dobson, Ostfeld and Samuel2002; Poulin and Mouritsen, Reference Poulin and Mouritsen2006; Burge et al., Reference Burge, Mark Eakin, Friedman, Froelich, Hershberger, Hofmann, Petes, Prager, Weil, Willis, Ford and Harvell2014; Byers, Reference Byers2020). However, these impacts may not necessarily involve disease, instead increases in parasite abundance can affect marine organisms in indirect ways, even organisms that are not part of a parasite’s life cycle. Here, we demonstrate that over a full year, periods of warmer temperatures are immediately followed by greater prevalence and abundance of infections by the trematode Copiatestes thyrsitae in its euphausiid hosts. The period between high temperatures and higher infection levels is from days to a few weeks, suggesting a rather rapid response of the parasite and an acceleration of this part of its life cycle as a function of higher temperatures. We found no such relationship between temperature and the number of third free-living stages, i.e. the stage that poses risks for seabirds. However, given the low numbers of free-living stages caught in our plankton net, such relationships are difficult to detect. Nevertheless, greater infections of euphausiids will invariably lead to the release of more free-living stages. Therefore, our results suggest that even short-term heatwaves can lead to high risks of seabirds becoming entangled with the C. thyrsitae filaments, with potentially dire consequences (see Claugher, Reference Claugher1976).
Until recently, Copiatestes spp. had only been reported infecting central to outer shelf pelagic fish species as definitive hosts in New Zealand, namely kahawai Arripis trutta, snapper Pagrus auratus, blue and silver warehou Seriolella brama and S. punctata, skipjack tuna Katsuwonus pelamis, jack and Murphy’s mackerel Trachurus novaezelandiae and T. murphy, and barracouta Thyrsites atun (Hine et al., Reference Hine, Jones and Diggles2000). If Copiatestes was not present in shallow coastal environments, then the risk of entanglement in coastal bird species would be negligible. However, Bennett et al. (Reference Bennett, Presswell and Poulin2023) recovered adult Copiatestes infecting small schooling coastal fish, i.e. mullet Aldrichetta forsteri and sprat Sprattus antipodum, meaning this parasite’s distribution extends to inshore areas. While our plankton net set-up filtered water from both incoming and outgoing tides, it is all ultimately neritic inshore water, further supporting the idea that Copiatestes poses a potential risk for coastal species beyond those in order Procellariiformes that have previously been implicated in filament entanglement.
The risk of Copiatestes entanglement will vary across bird species depending on body size, foraging ecology and behaviour (Imber, Reference Imber1984). Seabirds observed with anklets are typically small-bodied, consume euphausiids and/or exhibit feeding behaviours whereby their legs touch the water surface for extended periods of time (Ryan, Reference Ryan1986) (see anklet example Figure 2c–d). Smaller bodied birds may not have the physical strength to break up filaments once entangled (which are sometimes up to 60 mm long; Imber, Reference Imber1984), meaning they may be at higher risk of entanglement in future.
The majority of seabirds identified with Copiatestes anklets are small-bodied species that also consume krill and exhibit hydroplaning feeding behaviour (Ryan, Reference Ryan1986). This includes fairy prion (Pachyptila turtur, Tītī Wainui), broad-billed prion (Pachyptila vittata, Pararā), and the white-faced storm petrel (Pelagodroma marina, Takahikare-moana) (Claugher, Reference Claugher1976; Furness, Reference Furness1984; Imber, Reference Imber1984; Ryan, Reference Ryan1986). These birds all exhibit feeding strategies that involve surface foraging and flying close to the water surface during which they strike the water surface with their feet (Hernandez and Arroyo, Reference Hernandez and Arroyo2023). The white-faced storm petrel was the highest impacted species in the Copiatestes-associated mass mortality event in the Chatham Islands in 1970s, and the most frequently observed with anklets from a subsequent bird anklet survey in 1986 (Claugher, Reference Claugher1976; Ryan, Reference Ryan1986). Commonly referred to as the ‘Jesus Christ bird’ due to its apparent ability to walk on water while feeding (Southey, Reference Southey2022), this behaviour likely increases its exposure to free-living trematode stages.
An exception among small seabirds associated with anklets is the common diving petrel (Pelecanoides urinatrix), a pursuit diver. These birds use pattering behaviour to launch from feeding areas, propelling themselves in flight for distances up to 50 m (Ryan and Nel, Reference Ryan and Nel1999). Not only would this behaviour likely increase entanglement risk, but the fact that they seek out and predominantly consume Nyctiphanes australis as part of their diet in New Zealand and Australian waters (Fromant et al., Reference Fromant, Delord, Bost, Eizenberg, Botha, Cherel, Bustamante, Gardner, Brault-Favrou, Lec’hvien and Arnould2021) also contributes to their entanglement risk. While Copiatestes are present in coastal inshore ecosystems, there is no evidence of entanglements for inter- and subtidal bird species, like cormorants, oystercatchers and gulls. To date, only species from the order Procellariiformes are associated with trematode anklets. Procellariiformes are one of the most globally threatened avian groups (Croxall et al., Reference Croxall, Butchart, Lascelles, Stattersfield, Sullivan, Symes and Taylor2012), and in future, we can expect that for time periods up to one month post higher temperature spikes, bird species most at risk should be monitored for potential entanglement.
We found evidence that infected euphausiids are smaller in size than uninfected ones. This could be explained by either (1) if smaller euphausiids due to differences in behaviour are more likely to encounter free-living larval stages (shed from their first intermediate hosts) than larger euphausiids, or (2) this parasite is detrimental to the growth of their hosts. Considering the large size of Copiatestes within the host haemocoel, we assume that the second explanation is more likely. Larval parasite size is a trade-off between the benefits of being larger and the cost that a larger size imposes on their transmission success due to the negative impacts on host survival (Parker et al., Reference Parker, Chubb, Roberts, Michaud and Milinski2003). Copiatestes are not dependent on their euphausiid hosts’ survival for successful transmission to their fish definitive host (instead having a third free-living stage), meaning they may attain larger than typical sizes without the constraints that many other parasites experience.
How do increases in temperature lead to an increase of Copiatestes within the coastal ecosystem? The increase in presence of Copiatestes within euphausiids is most likely due to greater parasite production within the first intermediate host. Unfortunately, no first intermediate hosts have been identified for either of the two known Copiatestes species, worldwide. Based on the fact that most other trematodes use various molluscs as first intermediate hosts, we assume that the first intermediate host in this case is also a mollusc (Gibson et al., Reference Gibson, Jones and Bray2002). Warmer temperatures accelerate the asexual production of cercariae within the first intermediate hosts and trigger their release into the water column (Poulin, Reference Poulin2006). Monitoring outbreaks using larval stages as indicators may be a viable way to monitor this, and other problematic parasites in marine ecosystems, especially when it is not appropriate or ethical to directly monitor the animals that are being impacted.
Data availability statement
Samples of Copiatestes from the haemocoel of krill, Nyctiphanes australis are accessioned at Te Papa museum, under accession W.003620.
Acknowledgements
We thank all who assisted in plankton collection and processing, including: Shokoofeh Shamsi, Bronwen Presswell, Linda Groenewegen, Aaron Heimann, Brigette Kammlein, Adam Brook, Ellie Leinikki, Hannah Drury and Jean Mckinnon. The authors would like to thank and acknowledge local rūnaka and the komiti taoka tuku iho for their support of our disease screening process in Otago, and families of the Murihiku kaitiaki rōpū for their endorsement to work on Copiatestes. We’d like to thank Phil Sirvid at Te Papa Tongarewa Museum for accessioning parasite specimens and the constructive feedback from our two anonymous reviewers.
Author contributions
JB and RP conceived and designed the study. JB, ML, RL, SC and JEI conducted data gathering. JB performed statistical analyses. JB, RP and JK wrote the article with the input from ML, RL, SC and JEI.
Financial support
This project was co-funded by a Ministry for Business, Innovation and Employment (MBIE) Endeavour Fund awarded to Cawthron Institute, Emerging Aquatic Diseases, award number CAWX2207 and an MBIE participatory science platform project awarded to NZ Marine Studies Centre, University of Otago, Seasons in the sea: impacts of a changing climate on plankton communities of coastal Otago.
Competing interests
The authors declare there are no conflicts of interest.
Ethical standards
This work complies with the current laws and animal ethics regulations for research in New Zealand.
Open access
