# Colloquium on diatom-copepod interactions

Ga Paffenhöfer, A Ianora, A Miralto, Jt Turner, Gs Kleppel, Mr D alcalà, R Casotti, Gs Caldwell, G Pohnert, A Fontana, et al.

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## To cite this version:

Ga Paffenhöfer, A Ianora, A Miralto, Jt Turner, Gs Kleppel, et al.. Colloquium on diatom-copepod interactions. Marine Ecology Progress Series, 2005, 286, pp.293-305. 10.3354/meps286293. hal-03005512

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# Colloquium on diatom-copepod interactions

G. A. Paffenhöfer¹,*,+,*†, A. Ianora²,+,†, A. Miralto²,+ , J. T. Turner³,†, G. S. Kleppel⁴,†,
M. Ribera d'Alcalà²,†, R. Casotti²,†, G. S. Caldwell⁵,†, G. Pohnert⁶,†, A. Fontana⁷,†,
D. Müller-Navarra⁸,†, S. Jónasdóttir⁹,†, V. Armbrust¹⁰,#,U. Båmstedt¹¹,#, S. Ban¹²,#,
M. G. Bentley⁵,#, M. Boersma¹³,#, M. Bundy¹⁴,#, I. Buttino²,#, A. Calbet¹⁵,#, F. Carlotti¹⁶,#,
Y. Carotenuto²,#, G. d'Ippolito²,#, B. Frost¹⁰,#, C. Guisande¹⁷,#, W. Lampert¹⁸,#,
R. F. Lee¹,#, S. Mazza²,#, M. G. Mazzocchi²,#, J. C. Nejstgaard¹¹,#, S. A. Poulet¹⁹,#,
G. Romano²,#, V. Smetacek²⁰,#, S. Uye²¹,#, S. Wakeham¹,#, S. Watson²²,#, T. Wichard⁶,#

¹Skidaway Institute of Oceanography, Savannah, Georgia 31411, USA; ²Stazione Zoologica Anton Dohrn, 80121 Napoli, Italy; ³Biology Department, University of Massachusetts Dartmouth, North Dartmouth, Massachusetts 02747, USA; ⁴Department of Biological Sciences, University at Albany, State University of New York, Albany, New York 12222, USA; ⁵Marine Science and Technology, University of Newcastle upon Tyne, Newcastle upon Tyne NE1 7RU, UK; ⁶Max-Planck-Institut für Chemische Ökologie, 07745 Jena, Germany; ⁷Istituto per la Chimica Biomolecolare del CNR, 80121 Napoli, Italy; ⁸Institut für Hydrobiologie und Fischereiwissenschaft, 22767 Hamburg, Germany; ⁹Department of Marine Ecology and Aquaculture, Danish Institute for Fisheries Research, 2920 Charlottenlund, Denmark; ¹⁰School of Oceanography, University of Washington, Seattle, Washington 98195-7940, USA; ¹¹Department of Fisheries and Marine Biology, University of Bergen, 5020 Bergen, Norway; ¹²University of Shiga Prefecture, Hikone, Tokyo 164, Japan; ¹³AWI-Biologische Anstalt Helgoland, 27498 Helgoland, Germany; ¹⁴Academy of Natural Sciences Estuarine Research Center, St. Leonard, Maryland 20685, USA; ¹⁵Institut de Ciències del Mar - CMIMA (CSIC), 08003 Barcelona, Spain; ¹⁶Station Marine d'Arcachon, CNRS, Université de Bordeaux, 33120 Arcachon, France; ¹⁷Facultad de Ciencias, Universidad de Vigo, 36200 Vigo, Spain; ¹⁸Max-Planck-Institut für Limnologie, 24302 Plön, Germany; ¹⁹Station Biologique, CNRS, 29680 Roscoff, France; ²⁰Alfred-Wegener-Institut für Polar- und Meeresforschung, 27515 Bremerhaven, Germany; ²¹Hiroshima University, Higashi-Hiroshima 739-8528, Japan; ²²Environment Canada and University of Calgary, Alberta T2N 1N4, Canada

ABSTRACT: From 3 to 6 November 2002, a colloquium was convened at the Benthos Laboratory of the Stazione Zoologica Anton Dohrn on Ischia, Italy, with the goal of evaluating the present status of the effects of diatoms on their main consumers, planktonic copepods, and to develop future research strategies to enhance our understanding of such interactions. These included (1) toxic effects of diatom metabolites on copepods, particularly reproduction, and (2) nutritional effects of diatoms on juvenile to adult copepods. Key issues involved in the impact of diatoms on the dynamics of natural plankton communities *in situ* were also addressed. During the plenary session, the most recent advances on this topic were presented. The plenary session was followed by 3 working groups on (1) production of aldehydes by phytoplankton, (2) toxic and nutritional effects of diatoms on zoo-plankton, and (3) the chemistry of diatom defense, as well as of their nutritional quality. These working groups focused on suggesting future research needs for the different topics. As a result, several recommendations were outlined, including experimental studies. It became evident that interdisciplinary efforts are needed, involving chemists, oceanographers and experimentalists, since many of the biological observations under controlled conditions and *in situ* require an integrated approach, including chemical causation. Extensive field observations based on common protocols are also recommended for investigation of the intrinsic variability of such effects and their environmental controls. Laboratory experiments are seen to be essential for the full understanding of environmentally occurring processes.

KEY WORDS: Diatoms • Copepods • Toxicity • Nutrition

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# INTRODUCTION

Main contributors: J. T. Turner and G. S. Kleppel

Phytoplankton blooms have been a major issue in marine ecology for more than a century (Mills 1989 and references therein). Diatoms are often major components of these blooms, and have long been considered as principal components of planktonic copepod diets (Dakin 1908, Marshall 1924, 1973, Clarke 1939, Mauchline 1998), enhancing copepod fecundity and thereby supporting major fisheries (Ryther 1969, Greve & Parsons 1977, Cushing 1989).

The diatom-copepod link was fully accepted in biological and fishery oceanography by the mid-twentieth century. However, substantial data refuting the diatom → copepod → fish model began to emerge in the late 1980's and continued throughout the 1990's. Increased appreciation for the 'microbial loop' (Azam et al. 1983) and the importance of heterotrophic protists in grazing the dominant picoplanktonic phytoplankton somewhat diminished the importance of copepods as grazers of diatoms. Substantial, or even preferential, predation of copepods on heterotrophic protists and dinoflagellates (Sherr et al. 1986, Stoecker & Capuzzo 1990) seemed to reduce the importance of diatoms as copepod food. In fact, some copepods previously regarded as 'herbivores' have been shown to readily ingest heterotrophic protists and sustain fecundity on these food taxa (Ohman & Runge 1994), and such copepod production can contribute to larval fish recruitment during periods of low phytoplankton chlorophyll (Runge & de Lafontaine 1996). Additionally, copepod egg production was observed to be more closely correlated with heterotrophic protist and dinoflagellate biomass than with that of diatoms (Kleppel et al. 1991, Ohman & Runge 1994). Thus, by the 1990's, it was clear that the diatom-copepod trophic linkage was only part of a complicated planktonic food web, rather than a predominant food chain (reviewed by Kleppel 1993, Turner & Roff 1993, Verity & Paffenhöfer 1996).

In addition to the aforementioned studies, other information began to accumulate in the 1990's that questioned the beneficial role of diatoms as copepod food. Briefly, a body of evidence (reviewed by Paffenhöfer 2002, Ianora et al. 2003) indicated that ingestion of some diatom species by females of some calanoid species could decrease their reproductive success due to the presence of teratogenic, or reproduction-inhibitory chemicals in these diets. Unsaturated aldehydes (the term 'aldehyde(s)' is used in the text as an abbreviation to cover biologically active α,β,γ,δ- or α,β-unsaturated aldehydes) in some diatom species inhibited mitosis in developing copepod eggs and sea urchin embryos (Miralto et al. 1999), and induced

abnormal development of copepod nauplii in both the laboratory (Poulet et al. 1995, Carotenuto et al. 2002) and in the sea during periods of diatom abundance (Laabir et al. 1995a, 1998, Miralto et al. 2003, Ianora et al. 2004). Diets consisting of several species of diatoms have been shown to reduce egg viability in several species of copepods (Ianora et al. 1995, 1996, Ban et al. 1997, Lee et al. 1999, Starr et al. 1999, Lacoste et al. 2001). The reduction of egg hatching success is proportional to the length of exposure of egg-producing females to diatom diets (Laabir et al. 1995b, Turner et al. 2001), and to diatom concentrations (Chaudron et al. 1996).

As an alternative, some authors have argued that poor copepod egg production and egg viability result from nutritional inadequacies rather than teratogens in diatom diets of egg-producing female copepods (Jónasdóttir et al. 1998). Numerous correlations have been found between copepod fecundity and various elemental and biochemical components of maternal diets such as carbon, nitrogen, protein, carbohydrate, amino acid, and fatty acid content (Jónasdóttir 1994, Pond et al. 1996, Kleppel et al. 1998a,b, Koski et al. 1998). Schmidt & Jónasdóttir (1997) showed that copepod egg production increased when additional taxa were added to unialgal diets of nutritionally poor cyanobacteria. Copepod egg-hatching success was correlated to size and biochemical content (protein, carbohydrate, lipid) of eggs, and these parameters were correlated to biochemical compounds in natural food assemblages (Guisande & Harris 1995). Both copepod egg production and egg hatching have been correlated to dietary levels of fatty acids or amino acids in laboratory-cultured (Jónasdóttir & Kiørboe 1996, Guisande et al. 2000) and natural (Pond et al. 1996) diets. Other studies have revealed variable rates of copepod egg production on diets of natural phytoplankton dominated by various taxa (Tang et al. 1998, Irigoien et al. 2000a), with high variability in the effects on fecundity when diatoms were dominant (Irigoien et al. 2000b).

To consider the controversial issue regarding the relationship between diatoms and copepods, a meeting was convened at the Stazione Zoologica Anton Dohrn Benthos Laboratory, Ischia, Italy, from 3 to 6 November 2002. The goal of this meeting was to evaluate the present status of diatom-copepod interaction research, including unpublished results, and consider means by which to explore the effects of nutritional quality and the influence of secondary metabolites on the relationships between diatoms and copepods. Thirty-seven scientists from 10 countries participated. A consensus emerged from the meeting that a research agenda ought to be developed, aiming towards a comprehensive understanding of one of
the most fundamental and long-recognized interactions in the sea, which is that between diatoms and copepods.

In the following sections we will first present reports from 3 working groups: The first group, concentrating on phytoplankton, largely focused on aldehyde production and the mechanisms leading to such production. The second, concentrating on zooplankton, developed questions about how diatoms affect copepod reproduction and other population dynamics variables. The third group, concentrating on chemistry, had 2 points of interest, i.e. the chemistry of diatom defense and the nutritional chemistry of diatoms. In the last section we present considerations for future research, followed by concluding remarks.

## PRODUCTION OF ALDEHYDES BY PHYTOPLANKTON

Main contributors: M. Ribera d'Alcalà and R. Casotti

This section originates from a working group evaluating aldehyde production, and possible mechanisms initiating or modulating the formation of aldehydes from phytoplankton. The production of defense molecules against predation are widely known for both terrestrial (Rosenthal & Berenbaum 1991) and marine (McClintock & Baker 2001) higher plants. Much less is known about the production of these molecules in marine phytoplankton. Unsaturated aldehyde production has been shown to vary among different phytoplankton species, different genotypes of the same morphological species and different sites. Also, diatom aldehydes have been shown to differ in their toxicity, and those with an α,β-unsaturation and longer chain length are more toxic to animals than others (Adolph et al. 2003, Romano et al. 2003). However, it is not yet clear which phytoplankton populations produce aldehydes in nature, because relatively few species have been biochemically analyzed to date. Many of these are, indeed, species that form blooms, which reinforces the idea of a positive feedback between the production of aldehydes and increased diatom cell numbers at sea. On the other hand, species that do not form blooms have also been shown to produce the same or similar aldehydes, suggesting that chemical defense, per se, is not a sufficient requisite for increased population growth. Since all aldehydes require multi-step enzymatic catalysis, important questions arise about the genetic control of such processes. Such questions can be addressed in the near future using molecular tools, made possible by the recent sequencing and annotation of the marine diatom *Thalassiosira pseudonana* genome (Armbrust et al. 2004).

If the production of unsaturated aldehydes depends on a cell-controlled activation mechanism, their release should depend on a trigger. This trigger could be external (wound induction, presence of grazers, nutrient concentration, nutritional differences) or endogenous (growth stage, biochemical composition). Once chemical analytical methods advance, studies of the physiological control of aldehyde production at the cellular scale should be initiated, in order to dissect the endogenous mechanisms of aldehyde production by diatoms. Toxin production in phytoplankton is often related to different phases of the growth cycle (Imada et al. 1991, Schmidt & Hansen 2001), or even to cell-cycle phases (Bates et al. 1993, Bolch et al. 2002). It will have to be shown whether aldehyde production is higher in senescent cells or exponentially growing cells. The former would imply that grazers feeding at the end of a bloom are more affected than early-bloom grazers, while the latter would imply the opposite. Both scenarios would have strong implications for recruitment and trophic interactions at sea.

External factors triggering or modulating aldehyde production also need to be investigated, and light and nutrients are potentially important factors to consider. In freshwater chrysophytes producing the same aldehydes, physiological conditions, and light and nutrient availability, strongly modulate their production, which has strong implications for the phytoplankton community composition (Watson & Satchwill 2003). If similar results are obtained for marine bloom-forming species, this may represent a strong determinant for bloom dynamics. For example, the high-light conditions that diatoms experience when trapped in the surface layers of the water column as a consequence of stratification may have an effect on such reactive molecules. UV activation or modulation of toxicity has, in fact, also been observed for similar compounds (Wiegman et al. 2002).

If the production of such compounds is rewarded by a higher survival rate of the clones, the energy investment must be low; otherwise other phytoplankters would outcompete the producers due to reduced grazing pressure (Yoshida et al. 2003). Chemical defenses may also be effective against other competing autotrophs. For example, Casotti et al. (2001) suggested that diatom-derived aldehydes have an allelochemical function, since they arrest the proliferation of other diatom cells. If aldehyde production is related to the peak phase of a bloom, then aldehydes may be a control mechanism to prolong algal survival when nutrients become limiting. Such an altruistic behavior may be mediated by active mechanisms at the cellular level, such as programmed cell death (i.e. apoptosis), as has been demonstrated in *in vitro* experiments on different animal and plant models (Casotti et al. 2001,
2005, Romano et al. 2003). The release of aldehydes into the seawater in quantities that inhibit growth of competitors appears to be unrealistic (Pohnert 2000), but a quantitative assessment of aldehyde production during bloom conditions is still lacking. On the other hand, unsaturated aldehydes are produced by other algal groups in freshwater environments, in such high quantities as to cause serious socio-economic problems (Watson 2003). Unsaturated aldehyde production appears to be regulated by algal physiology, and therefore a possible role of these compounds as semiochemicals (i.e. pheromones, kairomones and allelogens) in freshwater habitats has been advanced (Watson & Satchwill 2003). Also in the ocean, there is evidence for the presence of secondary microalgal metabolites with a signaling function (Wolfe et al. 1997), and the question is whether diatom-produced aldehydes may also have such a role.

Diatoms, as a group, are major contributors to carbon fixation in the ocean (Nelson et al. 1995), and a significant fraction of diatom biomass is effectively transferred through the marine food web. Pathways therefore exist which allow diatom grazers to safely grow, reproduce and transfer their carbon to their consumers. This may be based upon avoidance or limited intake of toxic species, or on resistance mechanisms of copepod species. Unicellular grazers might be unaffected by diatom-derived aldehydes, or could even neutralize their effects. Such grazers have long been considered to be more effective than copepods in consuming phytoplankton (e.g. Frost 1987), and a recent study supports that view (Calbet & Landry 2004).

A thorough analysis of overlooked defense mechanisms will improve our understanding of the functioning of food webs and, thereby, of carbon drawdown by the ocean and the possible changes due to community shifts in the context of global change. It will also allow a better understanding of the impact of the diatom-copepod interactions on marine resources (fishery) and on the life strategies of pelagic and benthic organisms (marine biodiversity).

## TOXIC AND NUTRITIONAL EFFECTS OF DIATOMS ON ZOOPLANKTON

Main contributors: G. S. Caldwell and J. T. Turner

This section originates from a working group which mainly focused on formulating questions about the ways and means by which diatoms affect copepod reproduction, and other population dynamics variables. The general mechanisms considered were toxicity and nutritional inadequacy. Although some results point to the second issue, the information available on the nutritional value of diatoms *in situ* is still scarce. It

was emphasized that copepod species and also diatom species differ in their physiology, and that we possess hardly any knowledge as to how the ingestion of different diatom species would affect different copepod species, with a few published exceptions. The evidence that we have of a copepod species' feeding behavior in diatom blooms (e.g. Fessenden & Cowles 1994) is limited, because such blooms and associated particle qualities can vary widely in their composition, leaving room for a range of behavioral responses of the different copepod species. Various aspects of the known effects of diatoms on copepod reproduction and nutrition are presented in earlier and following sections. Here we limit the presentation to general questions and ideas concerning diatom-copepod interaction research, covering field and experimental observations.

How often are diatom toxicity and/or nutritional inadequacy associated with diatom blooms? To answer this question the quantifications needed over time would have to include copepod ingestion rates of the different bloom particles, subsequent egg production and hatching, and naupliar and copepodid development and mortality (post-embryonic fitness). Also, a thorough analysis of phytoplankton composition and abundance, and the phytoplankton species' chemical composition (see 'Chemistry of diatom defense' and 'Nutritional chemistry of diatoms') is needed. Answering the above-mentioned question would require oceanographic observations, as well as specific laboratory experiments simulating field conditions as closely as possible. Observations of Ban et al. (2000) demonstrated clear negative effects of diatom blooms, as reflected by the asymmetry of nauplii which had hatched under the bloom conditions. The field studies ought to be designed to understand the ecological significance of toxic molecules for natural copepod populations. Again, it is essential to distinguish between the effects of toxicity and nutritional value.

Following this, are different species of calanoid copepods, which are the main copepod consumers of diatoms, with different feeding strategies similarly affected by the same diatom conditions? Here, the possibility of detoxification should be considered. While Miralto et al. (1999) speculated as to the apparent lack of detoxification systems in copepods, Ianora et al. (2003) showed that the same diatom species could induce different effects in different copepod species. Benthic invertebrates have revealed pronounced species-specific variability in the sensitivity of their embryos to aldehyde toxicity (Caldwell et al. 2002). No inhibitory effects on reproductive and population growth parameters were observed following ingestion of the benthic diatom *Nitzschia closterium* by the
harpacticoid copepod *Tisbe biminiensis* (Pinto et al. 2001). Nutritional quality should affect growth and survival of nauplii and copepodid stages, as has been shown for *Calanus helgolandicus/pacificus*, where the ingestion of different diatom food species resulted in differing mortality rates and generation times (Paffenhöfer 1970). Similar findings were obtained by Carotenuto et al. (2002). The results of Koski et al. (1999) also revealed that food quality affects growth and development of calanoid copepods.

What are the mechanisms of transfer and accumulation of aldehydes and other toxic components, and their fate in growing copepods, as well as in eggs? There could be delayed effects, as has been shown for polychaete larvae cultured at very low aldehyde concentrations (0.0001 to 0.01 µg l⁻¹). These had hatched normally, but expressed pronounced anatomical deformities when they metamorphosed to nechtochaete larvae (Lewis et al. 2004). This, again, could vary with copepod species, but also with their physiological state, as well as their particle environment.

It was pointed out that the methods of quantifying rates of ingestion, reproduction, mortality, etc., as well as egg viability, ought to be standardized; this would be essential for a sound comparison of results originating from different investigators working at different locations on different species.

## CHEMISTRY OF DIATOM DEFENSE

Main contributors: G. Pohnert and A. Fontana

This section focuses on current and future strategies for the analyses of unsaturated aldehydes, the investigation of their biosynthetic origin and the regulation of their formation.

After the initial discovery of the inhibitory effect of unsaturated C10-aldehydes on the hatching success of copepods (Miralto et al. 1999), both mechanistic and methodological approaches were developed to gain an in-depth understanding of the 'defensive chemistry' of diatoms. During recent years, this has resulted in major progress towards the understanding of reactive aldehyde biosynthesis. Nevertheless, a detailed mechanistic and ecological understanding of the significance of diatom defense compared with the effects of overall food quality is yet to be achieved. Several different analytical approaches have been developed to detect unsaturated aldehydes in diatom cultures and in the natural environment (summarized in Table 1).

The data obtained to date from different diatom species and strains indicate that the formation of reactive aldehydes is not a universal property of all diatoms but is strongly variable among species and strains. For example, while *Thalassiosira rotula*, isolated from the Gulf of Naples, produces high amounts of 2E,4Z,7Z-

<table><caption>Table 1. Extraction and detection methods for reactive aldehydes from marine and freshwater diatoms. NMR: nuclear magnetic resonance</caption><thead><tr><th></th><th>Wittig-based derivatization<sup>a,b</sup><br>Metabolically unknown<br>samples (single species<br>and phytoplankton)</th><th>Metabolically known<br>organisms</th><th>Solid-phase<br>microextraction<sup>c,d</sup></th><th>HPLC-MS</th></tr></thead><tbody><tr><td>Amount of wet<br>weight required</td><td>2–5 g</td><td>800–900 mg</td><td>ca. 300 mg</td><td>ca. 300 mg</td></tr><tr><td>Information</td><td>Identification of<br>unknown metabolites<br>(assisted by NMR)</td><td>Identification of<br>known metabolites<br>by GC-MS</td><td>Identification of known<br>compounds with synthetic<br>standards using GC-MS<br>but difficult to quantify</td><td>Identification of<br>known compounds<br>with synthetic<br>standards</td></tr><tr><td>Time requirement</td><td>5 d</td><td>24 h</td><td>3 h</td><td>1 h</td></tr><tr><td>Sample preparation</td><td>Wounding/extraction/<br>derivatization/<br>chromatography</td><td>Wounding/extraction/<br>derivatization/<br>chromatography</td><td>Wounding/extraction/<br>chromatography</td><td>Wounding/<br>chromatography</td></tr><tr><td>Main advantages</td><td>Derivatized samples<br>are stable<br>Field measurements<br>possible<br>Unambiguous<br>identification<br>No standards required</td><td></td><td>Fast and sensitive<br>Suitable for screenings of<br>different cultures</td><td>Fast and sensitive<br>Reliable quantification<br>Identification of<br>polar oxylipins</td></tr></tbody><tfoot><tr><td colspan="5"><sup>a</sup>After d'Ippolito et al. (2002a); <sup>b</sup>after d'Ippolito et al. (2002b); <sup>c</sup>after Pohnert (2000); <sup>d</sup>after Watson et al. (1999)</td></tr></tfoot></table>
decatrienal and 2E,4E,7Z-decatrienal and traces of 2E,4Z-decadienal, *Skeletonema costatum* from the Adriatic Sea produces the volatile C8 aldehydes 2E,4Z-octadienal and 2E,4Z,7-octatrienal as major metabolites. Recent studies have shown that different aldehydes are derived from polyunsaturated C20 and C16 fatty acids (Pohnert 2000, d'Ippolito et al. 2002a,b, Pohnert et al. 2002), and that these compounds are produced not only by laboratory cultures but also by field-collected diatom species (A. Fontana & G. Pohnert unpubl. data). Yet, seston from marine and freshwater habitats and cultured diatom species have been identified that do not produce any of these or related oxylipins (T. Wichard, A. Fontana & G. Pohnert unpubl. data). This finding highlights the need for further screening of marine diatoms for their capability to synthesize unsaturated aldehydes. The laboratories in Jena (pohnert@ice.mpg.de), Napoli (afontana@icmib.na.cnr.it; romano@szn.it) and Calgary (swatson@ucalgary.ca) will perform these analyses and will give advice on sample preparation upon request.

Methods have been developed that provide tools for the investigation of the aldehyde production of diatom cultures or field samples and that can be used for a comparative screening of some of the major bloom-forming diatoms. In this regard, it is of primary interest to analyze samples of phytoplankton collected during algal blooms under well-known marine environmental conditions. Assisted by parallel studies of the *in situ* dynamics of diatom and copepod populations, this work will clarify not only the presence of aldehydes in major marine algal blooms, but also the ecological role of these compounds under natural conditions. This will allow estimation of the distribution of the potentially inhibitory species in the natural environment. A recent comparative study of *Thalassiosira rotula* from the Gulf of Naples and coastal California showed that, despite being genetically closely related and morphologically nearly identical, the Naples isolate produced high amounts of antiproliferative aldehydes (same as above), while the California strain completely lacked the ability to form these compounds (Pohnert et al. 2002). These 2 strains could be used in further comparative studies for the evaluation of the effects of oxylipins compared to the overall effects of food quality.

A major task in the near future will be the development of chemical analytical methods that will allow us to investigate processes in the copepod gut and tissue, in order to evaluate the possible uptake and distribution of reactive aldehydes towards target molecules, cells and organs. Correlative studies have shown that the effect of externally added aldehydes is the same as that observed after ingestion of aldehyde-producing diatoms. However, the high concentrations of 1 to 2 µg ml⁻¹ decadienal required to induce an effect, and the

unresolved question of local targeting of the metabolites in the copepods, do not allow the conclusion that these metabolites act directly and exclusively as defensive molecules to be made. Chemical methods, as well as bioassays and labeled probes, will be required in the future to bring a physiological understanding to this discussion. By using whole animals, it should be possible to investigate the distribution and location of reactive aldehydes after feeding. New strategies for the administration of reactive aldehydes with food will have to be developed. Whether this can be done, e.g. with microcapsules containing radioactive stable isotope-labeled samples of diatoms, will have to be established by collaboration among ecologists and analytical chemists.

Initial biosynthetic studies suggest that the production of these metabolites is triggered by mechanical damage (Pohnert 2000). After wounding, the release of eicosanoic fatty acids by a phospholipase A₂ is the first step of an enzymatic cascade involving a lipoxygenase and hydroperoxide lyase (Pohnert 2002). Studies of different diatom genera indicate that the biosynthesis of unsaturated aldehydes follows a similar pathway involving the same metabolic precursors and enzymes (Pohnert & Boland 2002, d'Ippolito et al. 2003). However, different diatom species can produce unsaturated aldehydes with differing biological activities, as has been shown for *Skeletonema costatum* and *Thalassiosira rotula*, which produce C7, C8 and C10 aldehydes (d'Ippolito et al. 2002a,b).

Future work will lead to a more profound understanding of how these molecules are released into the environment during growth, senescence and the feeding process, and will give additional information on the cell targets of the molecules. The influence of environmental conditions on the ability of diatoms to form reactive metabolites will also be addressed. To date, no information is available as to whether external chemical signals, such as light, nutrients or temperature, affect the quantity of aldehydes produced per cell. Such information would lead to a better understanding of regional differences in the defensive potential of diatoms. The greatest challenge for future years will be the search for additional or alternative primary and secondary metabolites that can influence the reproductive success of copepods.

## NUTRITIONAL CHEMISTRY OF DIATOMS

Main contributors: D. Müller-Navarra and S. Jónasdóttir

This section focuses on the differentiation of toxic effects from nutritive ones, i.e. compounds essential for copepod growth and development, with some suggestions.
tions for future research. The nutritional biology of marine copepods in general has recently been investigated by, e.g., Støtrup & Jensen (1990), Jónasdóttir (1994), Ederington et al. (1995), Kleppel & Burkart (1995), Pond et al. (1996), Guisande et al. (1999), and Klein Breteler et al. (1999). The focus of most of these studies was the effects of different algae on copepod performance. With regard to diatoms, monospecific diatom cultures have been shown to induce variable effects on copepod egg production and hatching (Jónasdóttir & Kiørboe 1996, Ban et al. 1997, Paffenhöfer 2002), ranging from being an excellent food source to being detrimental for copepods. The main issue is that in many studies it is not clear whether, or under which conditions, reduced egg production and hatching rates are due to toxins (e.g. certain aldehydes) in diatoms or to a nutritional inadequacy of a diatom diet.

From general knowledge of nutrition, it has been established that a whole variety of biochemicals and minerals must be supplied by the food. As a result, there is a high probability that a monospecific algal diet is nutritionally unbalanced or even deficient in 1 or more substances, and hence of inferior quality to a multispecies food mixture. Thus, it is easier for a monospecific algal culture to be nutritionally inadequate than the natural mixed diet copepods encounter in the field.

Nutritional chemistry studies of zooplankton in general have mainly focused on the fatty acid composition of the food (e.g. Müller-Navarra 1995, Jónasdóttir & Kiørboe 1996, von Elert 2002) and also, but to a lesser extent, on the amino acid composition (Kleppel & Burkart 1995, Guisande et al. 1999) and, recently, sterols (von Elert et al. 2003, Hassett 2004). Although considerable advances have been made in our knowledge of the nature of the biochemicals that might be important for limiting zooplankton growth and egg production during the last decade (Støtrup & Jensen 1990, Pond et al. 1996, Müller-Navarra et al. 2000, 2004, von Elert 2002, Becker & Boersma 2003), it is not yet clear what might be missing from the pure monospecific diatom cultures that seem to be of suboptimal food quality. Recent studies suggest that linolenic acid (18:3(n-3), von Elert 2002 for *Daphnia*) or cholesterol (Hassett 2004) may be underrepresented in certain diatoms. In contrast, although eicosapentaenoic acid, 20:5(n-3), is 1 important semi-essential nutrient for zooplankton growth, the concentrations in diatoms are generally very high, so these compounds are not expected to be limiting. However, evidence from aquaculture research indicates that easily degradable fatty acids like 20:5(n-3) have to be offered in a protected and bioavailable form, and that too high a concentration can have a detrimental effect on the consumer (McEnvoy et al. 1995, Coutteau et al. 1997, Jüttner 2001).

Separating potential toxic effects from nutritional inadequacy or deficiency is a major challenge in the nutritional biology of zooplankton. The effect of toxic and nutritionally deficient diets can both result in similar or identical phenomena (i.e. exhibit the same phenotypic features) in copepod reproduction, hence they cannot be easily distinguished. Separating the effects may at times be impossible if both alternative causes are not addressed in the measurements of factors in the field and in the design of laboratory studies. One of the simplest ways to differentiate between toxicity and nutritional deficiency is by means of an indirect test in which a deficient nutritional substance should have an enhancement effect when added as a supplement to a copepod culture, whereas a toxic substance should have a deteriorating (impairing) effect on the consumer when added. In addition, measurements of ingestion to evaluate selection are necessary. The substances in question have to be chemically characterized, added in a bioavailable form (e.g. as microcapsules), and in a way which does not lead to dilution of the food solution to be tested.

Additionally, the biochemicals that are potentially the most limiting resources need to be identified so that the above-mentioned experimental approach can be applied. Recent research has revealed that a balance of various nutritional components is important to ensure a high nutritional value of phytoplankton for zooplankton (Kleppel 1993, Anderson & Pond 2000). Even though, according to Liebig's law of the minimum, only 1 resource can be limiting at a time, a whole suite of essential nutrients should be required for somatic growth, egg production and hatching, because these 3 physiologically different production processes can have different nutritional requirements. In addition, because many nutritional substances can be stored in the copepod, experiments must ensure that these body reserves are depleted in the experimental animal before conclusions can be made about them being limiting under certain food conditions.

To fully understand the role of diatom quality in controlling copepod secondary production, only experiments and chemical analyses which integrate both toxic and nutritional aspects of food biochemistry will be successful in improving our understanding of the role of nutrition and toxicity in diatom-copepod interactions, and will resolve why some diatom species better support copepod population growth than others.

## FINAL CONSIDERATIONS FOR FUTURE RESEARCH

Several suggestions for future research on diatom-copepod interactions have been presented in the previous sections. In addition, we want to complement
these suggestions with some general thoughts, includ-
ing methods, to be followed by specific proposals for
future field and experimental efforts investigating
diatom toxicity to copepods and nutritional value of
diatoms, taking into account various recent observa-
tions on the interaction between copepods and their
food organisms.

General thoughts on methodology

To obtain insights into the relationships between
individual diatom species and the reproduction of indi-
vidual copepod species, proven methodologies should
be applied, following Ianora et al. (1995, 1996). The
methods used for comparative purposes, including
quantifying rates of ingestion, reproduction, mortality,
egg viability, and chemical analyses, should be stan-
dardized. The approach of Nejstgaard et al. (2001a,b)
is recommended for obtaining information about the
reproduction of individual copepod species feeding on
natural food spectra. This could be complemented by
the evolving methodology of Nejstgaard et al. (2003),
which reveals the ingested food species via DNA
markers in the gut contents. The latter methodology
should also be used in conjunction with that of Ianora
et al. (2004) when studying the extent to which juve-
nile stages are affected by ingested food taxa in situ.
Stage-specific ingestion experiments should apply a
single food taxon of proven 'good' quality as a control;
focus should be on whether juvenile stages select for or
against certain food types, and what biochemical com-
pound may characterize such food types. A promising
way to study these integrated effects on larval recruit-
ment in natural plankton is by the use of mesocosms
with minimally manipulated volumes (e.g. Nejstgaard
et al. 2001b).

Diatom toxicity to copepods

Most *in situ* observations of deleterious effects were
made when 1 or 2 species of diatoms dominated in
coastal regions (Ianora & Poulet 1993, Miralto et al.
1999, 2003, Ianora et al. 2004). To gain additional
knowledge of the *in situ* effects of major diatom blooms
consisting of 1 or 2 species, it may be useful to study
other coastal regions and shallow shelves known for
such or similar events over time. The following regions
could be promising: (1) Mississippi River plume, where
Turner & Tester (1989) found that, at certain times,
single diatom species such as *Skeletonema costatum* or
*Thalassiosira* spp. comprised 79 to 85% of all cells;
(2) the west coast of Scotland, where Marshall & Orr
(1930) reported a nearly monospecific bloom of *S*.

costatum, which provided food for emerging popula-
tions of *Calanus finmarchicus*; (3) Campeche Banks
in the Gulf of Mexico, with major diatom blooms
(Belousov et al. 1966); and (4) coastal waters off south
and western South Africa, with frequent diatom
blooms due to upwelling (e.g. Pitcher 1988). In addi-
tion, certain offshore regions, such as the Arabian Sea
during the SW monsoon (e.g. Smith 2001), and other
wind-driven upwelling areas, e.g. the NW coast of the
Iberian Peninsula, are known for pronounced diatom
blooms. Contrasting with diatom toxic effects, there
are also studies showing that diatoms have no or lim-
ited negative effects on the egg viability of various
calanoid copepod species (Pond et al. 1996, Irigoien et
al. 2002), or have only small effects (Miralto et al. 2003,
summer). These studies were carried out when the
diatom assemblage consisted of several species and
concentrations were lower than those observed in
early spring by Miralto et al. (2003). Observations
range from 'near-catastrophic' events of diatom toxic-
ity to copepod reproduction to cases in which the
effects were far less noticeable, if at all (e.g. Laabir et
al. 1995a). Unfortunately, the authors of most previous
studies did not quantify the particle types actually
ingested by the copepods, and no study correlating
aldehyde production with ingested food is known. As it
is possible that toxic diatoms are not ingested, the
claims of the absence of negative effects caused by
diatoms lack the basic information needed to substan-
tiate the conclusions. It should be further emphasized
that future *in situ* studies of food particle effects on
zooplankton need to quantify both the types and
amounts of food ingested (see Turner et al. 2001). This
was achieved in the following time-series study: A
series of 30 to 40 d mesocosm studies on the Norwe-
gian west coast (J. C. Nejstgaard unpubl. data) showed
a large variation in net production of copepods and
other zooplankton between seasons and years. The
mesocosms dominated by diatom blooms always sup-
ported a lower zooplankton net numerical and biomass
increase than simultaneous mesocosms dominated by
flagellates, despite the fact that both microplankton-
carbon biomass and copepod-carbon ingestion rates
were similar or higher in the diatom blooms. Experi-
mentally measured calanoid copepod egg produc-
tion and hatching rates were also lower in diatom-
dominated waters. In these experiments, the diet of the
calanoid copepods contained diatoms when present,
but the diatoms were never the preferred food.

There could also be differences in the susceptibility
of different calanoid copepod species to secondary
metabolites produced by diatoms. Irigoien et al. (2002)
observed relatively high hatching percentages of cer-
tain calanoid species, e.g. *Calanus finmarchicus*, in the
St. Lawrence estuary, even when diatoms were pres-
ent at high absolute and relative amounts (over 90% of the microplankton). However, they also reported low values for, e.g., *Temora longicornis* and *Calanoides acutus*, at concentrations and microplankton percentages similar to those above. It is hypothesized that not all species of calanoid copepods are sensitive to toxic substances produced by diatoms. Again, the uncertainty of ingested food particles prevents a thorough analysis and discussion when evaluating papers on this subject.

The main interest in this workshop was the effect of diatoms on copepods, especially under *in situ* conditions, when different taxa of phytoplankton and protozoans (mixotrophic and heterotrophic) occur. Protozoans generally make up only a small fraction of the unicellular plankton, yet they are preferentially ingested by copepods (e.g. Kleppel et al. 1991, Fessenden & Cowles 1994) and, therefore, could directly and indirectly affect their reproduction, growth, and mortality. Also, calanoids are known to reduce their total ingestion significantly when numerous food particles are encountered, as compared to when only 1 food type is available (e.g. Paffenhöfer 1984). The reduced food intake, most likely due to food selection processes, could lessen a potential effect of diatoms, since egg viability has been shown to increase with decreasing concentrations of ingested diatom cells (Chaudron et al. 1996) and when copepods are offered mixed diets (Turner et al. 2001). Thus, one could hypothesize that many calanoid copepod species would not suffer negative diatom effects under field conditions when diatom abundances are high because of alternative choices and/or lower diatom ingestion. This could be seen as an evolutionary effect deriving from altering perceptions in response to the chemical signals provided. We are still at an early stage in determining the potential release of toxic compounds by numerous species and strains of diatoms from various parts of the oceans. Among major efforts for the near future, a priority should be the development of a catalogue or atlas of diatom species and their occurrence, so as to assess their potential toxic effect on copepods.

## Nutritional value of diatoms

Most of the original studies of the nutritional quality of diatoms, as of algae in general, focused on their property to be easily ingested. In the last decade it became increasingly clear that their biochemical composition is also important for their quality as a food source for zooplankton including copepods.

Numerous studies of the fatty acid composition of diatoms have been conducted (e.g. Volkman et al. 1989, Viso & Marty 1993), while studies of other nutri-

tional components of diatoms, such as sterols and amino acids, are relatively few (but see Volkman et al. 1998 for sterols). Most studies of the specific nutritional needs of zooplankton have concentrated on the fatty acid composition of the food. While phytoplankton can synthesize a variety of so-called essential fatty acids (ω-6 and ω-3 polyunsaturated fatty acids), amino acids and sterols, copepods cannot synthesize these compounds, and must obtain them from phytoplankton to support growth, reproduction and survival. While some calanoid species can lengthen and shorten fatty acids (Sargent & Falk-Petersen 1988), we do not know if or how it benefits survival and growth.

A recent study by Hassett (2004) showed that addition of cholesterol to a diatom diet improved both egg production and hatching viability of *Acartia hudsonica*, whereas cholesterol supplementation did not affect egg production of *Centropages hamatus*. Cholesterol supplement of different diatom diets did not always result in production improvements. Thus, there appear to be species-specific differences in diatom sterols, as well as in copepod needs for dietary sterols. It is evident that the biochemical and, thus, the nutritional composition of phytoplankton changes as the availability of dissolved nutrients changes (Morris et al. 1983, Mayzaud et al. 1989). Feeding on diatoms at different growth phases results in different copepod egg production rates and egg viability (Jónasdóttir 1994, Jónasdóttir & Kiørboe 1996). Future studies ought to simultaneously focus on more than 1 type of nutrient in order to understand the different phases of growth.

Studies of the mortality rates of developing copepod populations offered different species of phytoplankton at similar and also at different concentrations have revealed effects of food species as well as of food concentration (Paffenhöfer 1970, Carotenuto et al. 2002 and references therein). Females of certain copepod species that had been reared at high diatom concentrations were rather sluggish when escaping from hydrodynamic signals after their final molt, as compared to specimens reared on diatoms at 1 order of magnitude lower concentration (G. A. Paffenhöfer unpubl. obs.). The females receiving a higher food concentration also experienced higher and earlier mortality. No information on the effects of satiation on copepod performance appears to exist. There is also very little information on the effects of the feeding history of early juvenile stages, as well as the feeding history of parent copepods, on their present performance. By comparison, a study of several generations of humans revealed that grandparents' eating habits can affect the health of generations twice removed: 'Grandchildren of well-fed grandfathers were 4 times as likely to die from diabetes' (Kaati et al. 2002). These
effects were considered to be due to eating behavior, and not genetics.

Quantification of molecular compounds in the gut (Nejstgaard et al. 2003) may provide insight into the recent feeding history of a single copepod, especially *in situ*. The biochemical composition of the body of a copepod (Lee et al. 1971) could inform us about the feeding history on longer time scales. From those data, in relation to the food types available, we may be able to determine a copepod species' approach to a 'healthy diet'. Future nutritional studies of diatoms should include looking for biochemical differences between diatom species and changes in composition with age, to improve our insight into nutritional effects. Experimental studies should include several groups of essential nutrients. A considerable amount of information is available on the biochemical composition of phytoplankton, and numerous studies have been conducted on reproductive and behavioral responses of copepods to different types of food. This published information is seen as a foundation to be applied to future studies of the nutritional effects of diatoms and other food organisms on zooplankton.

## CONCLUSIONS

The workshop was an attempt to assess the present status of research into diatom-copepod interactions, with emphasis on the effect of diatoms on copepod reproduction. We also considered the potential nutritional effects of food on growth and survival. It has to be kept in mind that the following sequence occurs in nature: a copepod encounters a wide range of potential food organisms (a spectrum), which is followed by food selection, then by the effects of the food on the copepod (whether as nauplius, copepodid stage, or adult male or female, or even through the following generations). All feeding stages are involved, and potential effects may not be highly visible or pronounced, as in some of the above-mentioned results concerning the effects of toxic diatoms on egg viability. We are at an early stage and need to chart out research plans to address the open questions and hypotheses, including those emerging as we proceed. It is clear that good communication among the research teams involved in diatom-copepod interactions will enhance progress. It is our hope that such communication will continue, reflecting the positive and collaborative attitude of the participants of our workshop.

*Acknowledgements.* We wish to thank the Stazione Zoologica Anton Dohrn for their generous financial support which provided traveling and logistics for many of the participants of this colloquium. We also thank the Benthos Laboratory of the Stazione Zoologica Anton Dohrn for hosting the meeting.

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