Oceanic physics at fine scale; e.g. eddies, fronts, filaments; are notoriously difficult to sample. However, an increasing number of theoretical approaches hypothesize that these processes affect phytoplankton diversity which have cascading effects on regional ecosystems. In 2015, we targeted the Iroise Sea (France) and evidenced the setting up of the Ushant tidal front from the beginning of spring to late summer. Seawater samples were taken during three sampling cruises and DNA-barcoding allowed us to investigate patterns of eukaryotic phytoplankton diversity across this front. First focusing on patterns of taxonomic richness, we evidenced that the front harbored a hotspot of eukaryotic phytoplankton diversity sustained throughout summer. We then detail the ecological processes leading to the formation of this hotspot by studying shifts in community composition across the Iroise Sea. Physical mixing mingled the communities surrounding the front, allowing the formation of a local ecotone, but it was cycles of disturbances and nutrient inputs over the front that allowed a decrease in competitive exclusion, which maintained a higher diversity of rare phytoplankton taxa. These processes did not select a specific ecological strategy as inferred by a trait approach coupled to our taxonomic approach. Instead the front favored higher richness within widespread strategies, resulting in functional redundancy. We detail how fine-scale ocean physics affect phytoplankton diversity and suppose that this interplay is a major control on regional ecosystems.
Photosynthetic microbes (i.e. phytoplankton) play key roles in marine ecosystems, driving biogeochemical cycles through their uptake of nutrients and carbon sequestration1,2, or producing the primary organic matter that supports marine food-webs3,4. The diversity of phytoplankton is of prime importance in these processes as richer phytoplankton communities are more efficient in nutrient uptake5, while larger phytoplankton assemblages promote the productivity and diversity of higher trophic levels6. Studying phytoplankton diversity is thus crucial to understand the interplay between microbes and the functioning of marine ecosystems. If previous studies have focused on phytoplankton diversity patterns at larger scale7,8,9, observations at the meso- and submeso-scale, of 100–0.1 km spatial and days to months temporal ranges10, remain scarce.
These studies showed that oceanic phytoplankton can be strongly affected by mesoscale (i.e. large eddies, fronts)11,12,13 and sub-mesoscale physical processes (i.e. smaller eddies, fronts, filaments)14. These processes have in common that they modulate the distribution of plankton, its access to resource and the resultant competition between taxa15,16. Despite numerous theoretical studies17,18,19,20, only few attempts were made to estimate the in-situ phytoplankton taxonomic diversity associated to meso and sub-mesoscale processes13,21, mainly because of the difficulty in locating and sampling these highly dynamic hydrographic features. Tidal fronts in coastal areas, ranging in between the sub-mesoscale and mesoscale, are recurrent22 and thus easier to target. They provide a great opportunity to investigate the in-situ interplay between small-scale ocean physics and the ecological processes driving phytoplankton diversity patterns.
Tidal fronts form seasonally in coastal ecosystems. In summer, the increase in atmospheric temperature warms surface seawaters, causing a stratification that prevents vertical mixing between the surface and bottom waters. In deep areas, tidal currents causes friction and mixing of the bottom water by interacting with the bathymetry but are not able to break the surface stratification23. Reversely, in shallow waters, the vertical mixing caused by bottom friction can reach the surface and prevents water stratification. Tidal fronts occurs at the frontier between (1) the deep, stratified, offshore water mass, and (2) the shallow, mixed, coastal water mass24. The sharp gradient in sea surface temperature at coastal tidal fronts makes them easier to survey25,26. Their development and seasonal dynamics have also been relatively well studied. As the summer progresses, both the coastal and offshore water masses become depleted in nutrients due to the uptake of phytoplankton and the reduction of nutrient inputs27,28,29. However, at fronts, tidal mixing still erodes and breaks the stratification. This results in a local upward vertical flux of nutrients from the offshore bottom water mass to the sunlit surface layer30,31,32, causing hydrographic discontinuities and outbursts of primary production over the front23,33,34. The effect of vertical mixing over coastal fronts is also strongly regulated by the spring/neap tide cycle (periodicity of ~ 14 days)35. Indeed, nutrients are mainly brought to the surface during the spring tides when tidal mixing is stronger, but it is during neap tides that re-stratification improves light availability which allows phytoplankton to grow in the vicinity of fronts34,36.
Phytoplankton’s community composition and diversity might undergo several ecological processes shaped by coastal tidal fronts37. Modulations in seawater conditions might favor different organisms with distinct environmental preferences (or niche), through the process called “Selection”. Selection might then affect the coexistence of phytoplankton species by modulating the timescale of competitive exclusion, i.e. the time needed by one selected species to outcompete the others under steady conditions38,39. Despite the small geographic scale at which coastal tidal fronts appear, they might also affect the movement (active or passive) and colonization of phytoplankton taxa across the offshore, frontal and coastal areas20, this process is called “Dispersal” (limitation or facilitation). Other ecological processes37, notably “Ecological Drift”; i.e. the random changes in community composition due to the inherent stochastic processes of birth, death, and reproduction; or “Diversification”; i.e. evolutionary generation of new species; are likely to have a smaller impact over coastal tidal fronts. In this study, we propose to investigate the drivers of phytoplankton diversity over a coastal tidal front.
The Ushant tidal front forms in the Iroise Sea and separates offshore waters coming from the Celtic Shelf40 from coastal waters moving northward along the French coast41. We sampled five stations distributed across this front along three time periods representing the cycle of formation and termination of the Ushant tidal front. We studied eukaryotic phytoplankton using DNA-barcoding in order to investigate diversity at a high resolution. We coupled this taxonomic approach to a trait approach to also study the functional diversity of phytoplankton. Traits represent any metric of an organism that informs its ecological strategy; i.e. strategy of resource acquisition, growth, reproduction or survival. Traits can underline the ecological strategy favored by selection processes42,43. We first detail patterns of taxonomy and richness across the coastal tidal front. We then make use of an approach that compares observed to random community turnovers (i.e. shifts in community composition) to infer the dominant ecological processes driving patterns of phytoplankton diversity. Finally, we investigate the ecological strategies selected by the hydrographic conditions of the front.
Materials and methods
Oceanographic context and sampling strategy
The Ushant tidal front forms in the Iroise Sea (Atlantic, Western France) and lasts from May to October28. Five stations distributed across the Ushant tidal front were sampled in our study; respectively from the open-ocean to the coast: O1, O2, F, C1 and C2 (Fig. 1a). The distance between stations was approximately 15 km, for a total transect of 58 km. The five stations were sampled three times during 2015, in early spring (10–12 March), early summer (1–3 July) and late summer (8–10 September). A sampling rosette equipped with Niskin bottles (10 L), a conductivity–temperature–depth probe (CTD) and a fluorescence sensor were used for profiling water temperature stratification, the chlorophyll a concentration and the Photosynthetically Active Radiation (PAR) over the water column (Fig. 1b,c). Water samples were collected at the surface (0–5 m) and, when present, at the deep chlorophyll maximum (DCM) identified by fluorescence profiling with the CTD. The water samples were triplicated by three repeated casts within 1 h and at the same geographic coordinates.
Seawater was processed with a sequential filtration approach in order to separate communities of micro-, nano- and pico-plankton (respectively > 10, 10–3 and 3–0.2 µm). Polycarbonate membrane filters of 47 mm in diameter were used for pore sizes of 10 and 3 µm, while polyether-sulfone sterivex were chosen for the pore size of 0.2 µm. For each sample, seawater was filtered until filter clogging, with volumes ranging from 2.7 to 5.6 L. The filters were frozen onboard in liquid nitrogen and later stored at − 80 °C until DNA extraction. An additional volume of water (0.5–1 L) was filtered through a 25 mm GF/F filter of 0.3 µm pore size, the filter was then placed in a cryotube and preserved at − 80 °C. These filters were later analyzed with High-Performance Liquid Chromatography analysis (Shimadzu) to quantify photosynthetic pigment concentration. These values were then used to calibrate the fluorescence sensor (Fig. 1b). Finally, 5–6 mL of seawater was filtered with a syringe holding a 25 mm GF/F filter of 0.3 µm pore size and preserved in ponyvials at − 20 °C. These last samples were used to estimate macronutrient concentrations using a Seal Analytical AA3 HR automatic analyzer following procedures described in reference44.
DNA barcoding was used to infer eukaryotic phytoplankton diversity at high resolution. Genomic DNA was extracted from the polycarbonate filters using the DNA extraction kit NucleoSpin Plant II from (Macherey-Nagel, Hoerdt, France). The V4 region of the 18S rDNA gene, a marker gene conserved but highly variable across the taxa of the protistan community, was amplified using PCR, performed with a taq polymerase (Phusion High-Fidelity PCR Master Mix with GC Buffer) and eukaryote-specific primers45. Library preparation was performed following the protocols of the NucleoSpin Gel and PCR Clean-up kits (Macherey-Nagel, Hoerdt, France). Sequencing was performed at the Genotoul platform using Illumina Mi-Seq (http://get.genotoul.fr/).
Bioinformatics consisted of a sequence quality filter using built-in modules of USEARCH46, singletons removal as performed in reference47, and sequence taxonomic annotation with the PR2 database48. Using Swarm249, similar variants of the amplified marker gene were clustered together to define Operational Taxonomic Unit (OTU), i.e. the species unit of DNA-barcoding. OTUs were annotated with the taxonomy of their most abundant variant. OTUs annotated to metazoan and pluri-cellular plants were removed. Further details about our DNA barcoding approach can be found in reference43, where bioinformatics have been performed on a larger dataset to improve error detection and OTUs clustering. Our dataset contains 33 060 OTUs accounting for 3.5 × 106 reads. Many OTUs were annotated with the same taxonomy, corresponding to 1028 unique taxonomic references. The taxonomic composition of this dataset can be investigated in Supplementary Fig. S1.
Eukaryotic phytoplankton diversity
All analyses were performed with the R software50 and the specific packages mentioned. Selection of OTUs representing eukaryotic phytoplankton was carried out by coupling our barcoding dataset with a trait database (available at www.seanoe.org/data/00405/51662/)43. The database is a custom trait annotation of the taxonomic references given to our OTUs (see DNA-barcoding section). After a literature review, we were able to identify 362 taxonomic references (from 1028) with an obligatory phototrophic lifestyle that represented eukaryotic phytoplankton51. We then created a sub-dataset of the 10,597 OTUs and 1.5 × 106 reads that were annotated to these 362 taxonomic references (representing respectively 32% OTUs and 45% reads in the initial dataset). This sub-dataset was used to study patterns of phytoplankton diversity. Sampling quality was evaluated by rarefaction curves (read vs. OTU number; rarecurve function of R package “vegan”52; Supplementary Fig. S2), and an estimate of richness saturation was calculated using the R package “iNEXT”53.
Eukaryotic phytoplankton richness (number of OTUs per sample or alpha-diversity) was computed for each of our 184 distinct samples, corresponding to distinct season (3), station (5), depth (2 when the DCM was sampled), size-fraction (3) and triplicate. Phytoplankton richness was first analyzed using boxplots across seasons, stations and size-fractions. Secondly, replicates and depth samples were merged and phytoplankton richness was computed again to represent the total phytoplankton richness across seasons and stations (15 samples). All statistical tests were performed on the dataset made of 184 samples. Patterns of phytoplankton richness were tested with the Kruskal–Wallis test, a non-parametric one-way analysis of variance. Differences in community composition (occurrence and proportions of OTUs across samples) were tested with a Permutational Multivariate Analysis of Variance using the Bray–Curtis distance (PERMANOVA; adonis function of R package “vegan”)52.
The spatial structure of phytoplankton diversity was studied by focusing on the occurrence of OTUs in each station within a season. OTUs were categorized in ‘shared’, when they occurred in more than one station within a season, or to ‘specific to station X’, when occurring only in station X. Phytoplankton richness was also studied according to its abundance. Rank abundance curves were built by calculating the total read number of OTUs in each season. OTUs were then sorted according to their total read abundance. In these rank abundance curves, OTUs from all size-fractions are merged, we note that this approach blurs the potential disproportionate abundance of size-fractions in the environment and the compositional nature of our DNA-barcoding dataset.
Community assembly of eukaryotic phytoplankton
To describe the spatio-temporal structure of eukaryotic phytoplankton, the number of OTUs shared between stations, within and across seasons, was computed with the R package “vegan” (betadiver function, metric α)52. To represent this metric, from now on called OTU-connectivity, we computed a network (with the R package “igraph”54) where nodes represent stations and edges width represent the number of OTUs shared between two stations. Surface and DCM samples were distinguished in this analysis. We tested if the sampling effect between seasons (different phytoplankton richness across seasons) affected OTU-connectivity by comparing the observed OTU-connectivity with the OTU-connectivity in a sub-dataset with a curated number of OTUs by season (see the experimental procedure in Supplementary Fig. S3). The correlation between the connectivity matrices (pairwise comparison of the number of OTUs shared between samples) of the original and the curated dataset were studied with the Spearman rank correlation. Further analyses of the connectivity network can be found in Supplementary Figure S4.
To quantify the ecological processes that constrained phytoplankton community patterns across the Ushant tidal front we followed the approach of reference55. The method has already been reviewed37, further details are given in Supplementary Figure S5. Briefly, the method is based on the comparison of observed community turnovers (shift in composition across samples), phylogenetic turnovers (shifts in composition weighted by phylogenetic similarity between taxa) and turnovers expected by chance (in null-models), in order to estimate whether the differences between pairs of communities are explained by Dispersal, Selection, or Ecological Drift37. The implicit hypothesis is that phylogeny is a proxy for niche divergence between taxa, so phylogenetic turnover can then be used to infer niche-based selection. This hypothesis has seldom been tested for phytoplankton56 and thus, before applying this method, the relationship between OTU-OTU phylogeny and trait-based distances was tested (Supplementary Fig. S5). The phylogenetic distance and tree were computed with R following reference57. The method comprises a sequence multiple-alignment (here eukaryotic phytoplankton V4 sequences of the 18S rDNA) and the computation of a neighbor-joining tree fitted to a GTR + G + I maximum likelihood tree. Phylogenetic turnover was estimated with the ß-Mean-Nearest-Taxon-Distance (ßMNTD) (comdistnt function of R package “Picante”58). Composition turnover was computed using Jaccard’s dissimilarity index59. 999 null-models were computed with built-in R functions, using random shuffling of the phylogenetic tree labels for null-models of phylogenetic turnover (ßMNTD)55 and using the Raup-Crick metric (RC) for null-models of composition turnover59. The ß-Nearest-Taxon-Index (ßNTI) was computed as the difference between the observed ßMNTD and the mean of the ßMNTD null-models. The inference of the dominant ecological process between a pair of sample was carried out following Refs.55,60; with |ßNTI| > 2 interpreted as a dominance of selection, |ßNTI| < 2 and |RC| > 0.95 interpreted as a dominance of dispersal and |ßNTI| < 2 and |RC| < 0.95 interpreted as a dominance of ecological drift. Negative values of ßNTI and RC represent communities that are more similar than expected by chance, selection and dispersal were thus considered ‘homogenous’ or ‘homogenizing’, at the contrary positive values represent communities where ‘variable selection’ and ‘dispersal limitation’ favor dissimilarity (higher than expected by chance). Compositionality, the phylogenetic uncertainty of a tree based on short amplicon size and potential biases in local richness are recognized limitations to this approach55. Therefore a safe approach was adopted by using non-weighted-metrics, testing the relationship between phylogeny and traits (Supplementary Fig. S5), and testing whether variable richness across seasons affected our interpretations (Supplementary Fig. S4).
To investigate the environmental variables forcing selective processes on phytoplankton communities, the significance of the difference in phylogenetic turnovers (ßMNTD) across environmental variables were tested with a PERMANOVA. Size fractions were distinguished in this analysis.
Functional richness of eukaryotic phytoplankton
After investigating the patterns of taxonomic richness and composition of eukaryotic phytoplankton, we studied its functional richness with an innovative approach61. This method uses the estimation of species occurrence across samples and a trait-table describing these species, to compute functional richness. Using our trait database43, we generated a sub-dataset of 287 eukaryotic phytoplankton taxonomic references (out of 362) that were well annotated with the following morphological and trophic traits (12): SizeMin, SizeMax, Cell Cover, Cell Shape, Presence of Spicule, Cell Symmetry, Cell Polarity, Coloniality, Motility, Ingestion method, Symbiosis type and Resting Stage during the life cycle. These 287 taxonomic references constituted a sub-dataset of 7106 OTUs and 1.2 × 106 reads (representing respectively 67% of OTUs and 80% of reads in the original phytoplankton dataset). To compare taxonomic and functional richness at large, OTUs occurrence was merged across seasons (3) and stations (5). Functional richness was then computed based on (a) this sub-dataset (7106 OTUs/15 samples) transformed in a presence–absence table, and (b) a trait table describing the 7106 OTUs of the sub-dataset (12 traits). Functional richness was computed with built-in R functions using Gower distance and Principal Coordinate Analysis (PCoA)61.
Finally, to investigate the ecological strategies of phytoplankton displayed across the Iroise Sea, we computed Gower’s Distance and the Complete Linkage’s method of Hierarchical Clustering62 on our trait table of 7106 OTUs and 12 traits (see this section). This approach identified 9 clusters of OTUs with similar trait combinations, thus representing ecological strategies (Supplementary Fig. S6). We focus on the distribution of these strategies in September by assuming that by the end of summer the accumulated selection processes might have narrowed the communities to few strategies.
By analyzing physicochemical variables measured in the Iroise-Sea during a 2015 oceanographic campaign (Fig. 1a–c), we evidenced the Ushant tidal front in summer (July and September), with the most offshore stations (O1, O2) being stratified, as demonstrated by the temperature profiles, while temperature was more homogenous across depth in the coastal stations (C1, C2). As expected, the front was not yet established in March. Contrasting with the nutrient-replete waters of early-spring (March), the surface summer waters of the Iroise-Sea presented a marked nutrient depletion, at the exception of the waters at station F, and to a lesser extent in the coast at C1 and C2 (Fig. 1b). Phytoplankton production persisted at the DCM of the most offshore stations especially at station O2 in September, suggesting that phytoplankton at station O2 might benefit from the nutrient inputs and is close to the thermal front (Fig. 1b). However, lower nutrient (Fig. 1b) and light availability (PAR, Fig. 1c) might have constrained phytoplankton productivity in the rest of the stations. Station F presented a weaker stratification throughout summer and significant nutrient inputs at surface in September (Fig. 1b). This suggests that station F was the closest station to the front, although the front’s position probably oscillated between station F and O2 depending on tidal cycles and wind conditions.
Phytoplankton community composition
In this section, we first present the patterns of phytoplankton taxonomic groups across seasons (Fig. 2). The total phytoplankton read abundance (1.5 × 106 reads) was dominated by Bacillaryophyta (i.e. diatoms, 36% of the total phytoplankton read abundance) and Dinophyta (i.e. dinoflagellates, 31%), that dominated micro-plankton. Chlorophyta (25%), Cryptophyta (5%) and Dictyochophyta (1%) were more abundant in the nano- and pico-plankton. Organisms from Pelagophyta (1.5%) were observed homogenously across all size fractions but appeared mostly in September in the offshore samples. As is typical for sequencing surveys63, DNA from organisms of specific size-fractions slightly contaminated other fractions due to cell-breakage (e.g. dictyochophytes, pelagophytes usually found in the pico-plankton or diatoms and dinoflagellates usually found more dominant in the micro-nano-plankton). The variability in community composition within triplicates was not significant (PERMANOVA, R2: 0.1 with 9999 permutations). More surprisingly, across stratified waters in July and September, no significant differences were found between the OTU compositions at surface and at the DCM (PERMANOVA, R2: 0.03 with 9999 permutations). Vertical mixing in the surface layers thus appeared sufficient to mix the communities from the DCM and the surface, making selection at different depth undetectable with our methodology.
In March, phytoplankton was dominated by diatoms in the micro- and nano-plankton (respectively above 75 and 40% of the total phytoplankton abundance), Cryptophyta appeared above 10% in both the nano- and pico-plankton, while Chlorophyta dominated pico-plankton (above 75% by sample, Fig. 2). During this period, the relative abundance of the phytoplankton taxa was homogenous across the Iroise Sea (Fig. 2). In July, the community was dominated by dinoflagellates in the higher size-fractions. However, diatoms remained abundant in the most coastal area (Fig. 2). Among pico-plankton, Chlorophyta was the most abundant taxa but dinoflagellates and diatoms also appeared consistently in this size-fraction. Pico-plankton was relatively homogenous over the Iroise Sea except for the most coastal station (C2) that showed a stronger domination of Chlorophyta (Fig. 2). In September, the spatial structuration was stronger across all size fractions. Micro- and nano-plankton were dominated by diatoms and to a lesser extent by dinoflagellates (Fig. 2). This season was mainly characterized by the presence of Pelagophyta and Dictyochophyta in the most offshore stations (above 10% and 3% in O1 and O2) with Pelagophyta appearing across all size fractions while Dictyochophyta appeared mostly in the nano-plankton (Fig. 2). The frontal and coastal stations (F, C1 and C2) showed noticeable abundances of Cryptophyta in the nano-plankton (above 10%). Across pico-plankton, stations were also divided into two groups, one with the coastal and frontal stations (F, C1 and C2) where Chlorophyta strongly dominated, and one with the offshore stations (O1 and O2) where Chlorophyta, Pelagophyta, diatoms and dinoflagellates were more evenly distributed (Fig. 2).
Patterns of phytoplankton richness
In this section, we investigated patterns of eukaryotic phytoplankton richness using the total number of OTUs as a proxy. Rarefaction analyses indicated that reaching near saturation for the eukaryotic phytoplankton of the Iroise sea’s (13,659 OTUs) would require between 500 and 600 samples following our strategy (Supplementary Fig. S2). With 10,597 OTUs, our study did not saturated diversity but represents the diversity patterns of the most abundant share of the eukaryotic phytoplankton communities sampled. We detail the non-extrapolated richness retrieved in our original dataset.
The variability of eukaryotic phytoplankton richness (i.e. the number of phytoplankton OTUs in a sample) in the Iroise Sea throughout 2015 is presented in Fig. 3a (for all 184 samples considered independently). Phytoplankton richness was significantly higher in micro- and nano-plankton than in the pico-plankton (P < 0.0001, Kruskal–Wallis test). Micro- and nano-plankton presented the highest richness (maxima of 970 and 729 OTUs respectively) whereas pico-plankton presented lower values (maximum of 504 OTUs). Phytoplankton richness also declined significantly along seasons (P < 0.0001, Kruskal–Wallis test; Fig. 3a) and this decline was strongest for the micro- (maxima of 970, 467 and 381 respectively in March, July and September) than for nano- and pico-plankton (maxima of 729 and 504 OTUs in March, to 529 and 270 OTUs in September, respectively for nano- and pico-plankton). Among stations that presented DCMs and in agreement with results on community composition, no significant difference existed in phytoplankton richness between DCM and surface samples (P = 0.1, Kruskal–Wallis test).
To better represent the spatio-temporal structure of phytoplankton richness, OTU counts from replicates, size-fractions and depths were merged (15 samples; Fig. 3b). As expected, richness increased across stations and seasons (Fig. 3b). This increase was more influenced by merging replicates and size-fractions than by merging samples from different depths, in accordance with tests showing no significant difference in phytoplankton composition (PERMANOVA, R2: 0.03 with 9999 permutations) and richness (P = 0.1, Kruskal–Wallis test) between superficial and DCM samples. Along seasons and parallel to a depletion in nutrients, the total phytoplankton richness declined, with maxima of 2628, 2066 and 1999, respectively in March, July and September (Fig. 3b). However, across stations there existed discrepancies to this pattern. In July, the stations nearest to the front (F and O2) were richer than the others (above 2000 phytoplankton OTUs in comparison with values lower than 1700 OTUs in other stations), while in September, station F showed the highest phytoplankton richness (1999 OTUs in comparisons with < 1100 OTUs elsewhere). Consequently, richness was significantly higher at station F over summer (P < 0.005, Kruskal–Wallis test based on the complete dataset of 184 samples), highlighting that the front represented a hotspot of phytoplankton diversity.
To investigate the composition of this hotspot, OTUs were sorted according to their occurrence in each station by season (Fig. 3b). Across July and September, when the front was established, Station F showed a significantly higher richness of ‘shared’ OTUs (P < 0.01, Kruskal–Wallis test based on the summer-only dataset, 140 samples). When cumulated, its proportion of ‘specific’ OTUs reached 50% of phytoplankton richness in September (station F: 997 ‘Specific’ + 1002 ‘Shared’ OTUs), the highest value across stations and seasons (Fig. 3b). Next, the ‘shared’ OTUs constituted the larger part of the ‘abundant’ community (OTUs > 0.1% of the total read number of phytoplankton OTUs by season; Fig. 3c). ‘Specific’ OTUs were present in the ‘low abundance’ community (0.1–0.01%) and numerous in the ‘rare’ community (< 0.01%; Fig. 3c). This indicated that the most abundant species had a larger dispersal (and detection potential), while the distribution of rarer taxa was sparser and spatially structured. The numerous ‘specific’ OTUs found at Station F in September thus had low abundances. The rank abundances also highlighted that the shrinking of phytoplankton richness across seasons was mostly due to the rare community (with 4092, 3262 and 2462 of rare OTUs respectively in March, July and September; Fig. 3c).
Phytoplankton turnovers, dominant ecological processes and environmental drivers
As a preliminary step to this section, we tested if OTU-connectivity (Fig. 4a) was influenced by the decreasing number of OTUs by season observed in Fig. 3, a potential bias in our analysis. The observed diversity patterns were conserved in a dataset with a curated number of OTUs by season (Spearman Rank Correlation of 0.99; Supplementary Fig. S3), indicating that OTU-connectivity was not influenced by the varying number of OTUs retrieved in each season, we thus detail the observed patterns. First, OTU-connectivity was significantly higher within seasons than across seasons (Fig. 4a; Supplementary Fig. S4, P < 0.001, Kruskal–Wallis test), illustrating a seasonal renewal of the phytoplankton community. Secondly, the connectivity between stations within a season significantly decreased from early spring to late summer (Fig. 4a; Supplementary Fig. S4, P < 0.001, Kruskal–Wallis test), highlighting the progressive separation of communities across stations. Finally, cross-seasonal connectivity indicated significant patterns: (1) in March, all stations were rich and phytoplankton OTUs were widespread (high connectivity intra-season), (2) in July, some OTUs found in March still occurred in the coastal and the frontal stations (C2 and F, see the cross-seasonal links in between March and July), indicating a strong renewal of the phytoplankton community elsewhere, and 3) in September, OTUs sustained from March and July were found in a greater extent at the front (cross-seasonal link in between July and September). As a consequence, OTU-connectivity at the frontal station was higher than at other stations, both within (Fig. 4a; Supplementary Fig. S4, P < 0.001, Kruskal–Wallis test) and across seasons (Fig. 4a; Supplementary Fig. S4, P < 0.001, Kruskal–Wallis test).
The null-model approach based on phylogenetic and compositional turnovers supposed that eukaryotic phytoplankton was strongly affected by selection (Fig. 4b). Out of 5551 pairwise community comparisons, 5545 were dominated by Homogenous Selection, 3 by Dispersal Limitation, 2 by Homogenizing Dispersal and 1 non-dominated (supposedly representing Ecological Drift). The domination of Homogenous Selection supposes that the OTU-composition across stations remained very similar throughout our sampling (as evidenced by OTU-connectivity, Fig. 4a), and followed the same selection process over time. The pairwise community comparisons where selection was relaxed (i.e. where |ßNTI| < 2) were all (6) within the micro-plankton and 4 involved the frontal station. Non-selective pairwise comparisons also evidenced the increasing structuration of the micro-phytoplankton across the front in summer (Fig. 4b), with dispersal limitation reducing the similarity between the offshore and the coast (O2 in March, C1 in July), and between the coast and the frontal station (C1 in July, F in September). However, the frontal station, richer in OTUs, also contributed through dispersal to the community composition on the offshore side of the front (O1 in July, O2 in September, F in July).
The factors driving phytoplankton selection were investigated using PERMANOVA between phylogenetic turnovers (ßMNTD) and the environmental factors during our cruises. Two PERMANOVAs were computed, both showed that our environmental factors explained between 50 and 62% (across PERMANOVAs and size-fractions) of the turnovers variance, supposing that the rest of the variance was explained by unmeasured factors. The first PERMANOVA highlighted a strong correlation between temperature and phytoplankton phylogenetic turnovers (R2 for the micro: 0.24, nano: 0.27, picoplankton: 0.28 with p values of 0.001); in agreement with our sampling strategy targeting a seasonal increase in temperature and a thermal front (Fig. 1). To elaborate on this result, a second PERMANOVA was computed without temperature (Fig. 5). In this analysis, nutrients correlated with phytoplankton turnovers, most notably nitrate + nitrite, globally decreasing across seasons except at the front (R2 for the micro: 0.22, nano: 0.27, picoplankton: 0.24 with p values of 0.001), ammonium, globally increasing with the summer remineralization of the spring bloom (R2 for the micro: 0.21, nano: 0.08, picoplankton: 0.07 with p values of 0.001), but also to a smaller extent silicate, mostly impacting diatoms’ growth (R2 for the micro: 0.13, nano: 0.09, picoplankton: 0.08 with p values of 0.001). This analysis illustrates the strong selective effect of water temperature and nutrient availability on the phytoplankton community of the Iroise Sea.
Phytoplankton functional diversity
Using a trait database adapted to our DNA barcoding dataset, we first tested if the hotspot of phytoplankton diversity also corresponded to a higher number of ecological strategies. Secondly, we investigated if the observed selection pressures resulted in distinct sets of ecological strategies across the front by the end of summer.
Functional richness, ranging between 0 and 1, was high (> 0.7) supposing that all stations and seasons presented several distinct phytoplankton strategies (Fig. 6a). Contrary to taxonomic richness, the functional richness of phytoplankton did not show its highest values in March (between 0.79 and 0.83) but in July and September (ranging between 0.87 and 0.88). These high values were observed in the offshore and frontal area in July (O1, O2, F) but only at the most offshore station O1 in September (Fig. 6a). Despite a taxonomic richness twice lower than observed at the frontal station (Fig. 3), the most offshore area presented equivalent or higher functional richness than the frontal station. This suggests that the hotspot of diversity found at the front in summer presented a high number of taxa with similar ecological strategies, i.e. functional redundancy. Overall functional redundancy also explained the absence of correlation between the taxonomic and functional richness of eukaryotic phytoplankton (Fig. 6b).
By studying the distribution of 9 distinct ecological strategies of phytoplankton (Supplementary Fig. S6) across the front in September, we evidenced that the front did not select a specific ecological strategy (Fig. 7), despite a higher number of OTUs. Only the Rhizarians (ES 1); a very distinctive ecological strategy composed of OTUs with silica or strontium sulfate covers, spicules, able of phagotrophy and often carrying photosymbionts; showed a cross-frontal pattern with an increase of the OTUs number towards the open ocean (Fig. 7), despite overall low abundances in our dataset.
Phytoplankton community composition
The Iroise Sea presented various environmental conditions that influenced the proportions of phytoplankton taxa due to differences in environmental niche and fitness.
Diatoms dominated the larger size-fractions (micro- and nano-phytoplankton) during early-spring (March) when light only started to become available in the nutrient-rich and mixed Iroise Sea. This supports evidence that diatoms are good competitors under high nutrient concentration64. The summer conditions represented nutrient-depleted and stratified waters and were dominated by dinoflagellates. Dinoflagellates have indeed better competitive abilities in such conditions (e.g. swimming to persist in the euphotic zone when mixing is low, or mixotrophic capabilities to compensate for low nutrient concentration)64,65,66. In summer, the coastal and frontal waters were markedly less depleted (NOx ~ 2 µM) than the open-ocean waters, these conditions thus helped to maintain a diatom community mixed with dinoflagellates. The smaller Cryptophytes occurred in the nano-phytoplankton and showed ubiquitous distribution in early-spring (March) as well as high proportions at the coast in September. Because of their size, Cryptophytes have lower light requirements67 and tend to favor coastal ecosystems63, which could explain their occurrence in March and restraint at the coast in September when the rest of the Iroise Sea presented more oceanic influences (Fig. 1). Finally, the pico-phytoplankton was dominated by Chlorophytes, as is typical in coastal ecosystems63. Due to their tiny size68, Chlorophytes have even lower requirements which allow them to grow in winter or in DCMs where the growth of large micro-phytoplankton organisms is greatly lowered67. In the Iroise Sea, light limitation also occurs in the shallower coastal area during summer due to vertical mixing and turbidity69,70, which again favored Chlorophytes in these areas (Fig. 2). In contrast, the lower proportion of Chlorophytes at the DCM of offshore stations, another light-limited environment, could be explained by the competition with other pico-eukaryotes. Indeed, both Pelagogphytes71 and Dictyochophytes72, observed in the most offshore areas, have a marked preference for deeper and stratified water masses.
Our environmental analysis (Fig. 5) partly agreed with these theoretical interpretations64,65,68. Nutrients and temperature were shown to be major drivers of phytoplankton selection (Fig. 5), but light availability (estimated with P.A.R.) did not seem to affect phytoplankton community patterns. This discrepancy can be explained by the fact that our measurements represent only snapshots of the environment and do not inform on its history (e.g. the past and daily exposure to light). Estimation of grazing pressure is also missing in our study but is likely to influence phytoplankton community patterns73. Nevertheless, our DNA barcoding approach detailed communities of eukaryotic phytoplankton under strong selective pressure, and this with a high taxonomic resolution illustrated by the addition of less-studied organisms like dictyochophytes or pelagophytes.
The formation of a phytoplankton diversity hotspot
Selection processes also affected eukaryotic phytoplankton richness. Here, we detail the ecological processes leading to these patterns by focusing on taxonomic richness and turnovers of eukaryotic phytoplankton.
First, phytoplankton richness decreased significantly across seasons. Although our turnover approach would benefit from a higher resolution (spatial, temporal, phylogenetic and in the estimation of taxa’s abundance), it provided us with arguments to say that homogenous selection was the dominant ecological process affecting phytoplankton communities (Fig. 4b). This process dominates when communities appear in the same selective environment and when selection is strong60. In the geographic scale of our study (58 km), the Iroise Sea thus represented a homogenous pool of phytoplankton OTUs undergoing similar selection pressures. Additional analyses highlighted that temperature gradients and nutrient availability were important drivers of selection (Fig. 5), as is customary for phytoplankton taxa64,65. Under such continuous selection, the competition between taxa is predicted to increase, fewer taxa with better abilities under selection will survive38,39, resulting in the overall shrinking of phytoplankton richness that we observed in the Iroise Sea towards the end of summer (Fig. 3). Nutrient-driven selection probably explained why the shrinking of phytoplankton richness appeared mostly in the larger size-fractions, as the smaller organisms are usually more resistant to nutrient depletion67.
In contrast with the rest of the Iroise Sea, the frontal area maintained a higher phytoplankton richness across summer (Fig. 3), resulting in a phytoplankton diversity hotspot. Studying phytoplankton turnovers, we evidenced that selection was more relaxed over the front (Fig. 4b). Indeed, as in other fronts in summer, tidal mixing allows the upwelling of cold and nutrient-rich waters up to the surface of the Ushant tidal front31 (Fig. 1b). These nutrient inputs could have lowered selection and the resulting competitive exclusion, thus favoring higher richness. However, under continuous, or undisturbed, nutrient conditions, competitive exclusion between phytoplankton taxa is also predicted to increase73. Over the Ushant tidal front, disturbances originating from the spring/neap tide cycle and wind-induced perturbations are known to affect nutrients and light availability for surface phytoplankton34,35. In a mechanism reminiscent of the Intermediate Disturbance Hypothesis74,75, we speculate that the coupled cycles of tide-induced disturbances and nutrient inputs lowered competition locally, which helped to maintain a phytoplankton diversity hotspot over the front. It must be emphasized that these disturbances act at a short time scale, tangible with our yearly survey, but cannot prevent competitive exclusion and extinction in the long term76.
Focusing on the origin and connectivity of OTUs in the Iroise Sea, we evidenced that the front harbored a higher proportion of phytoplankton OTUs from surrounding areas (Figs. 3b, 4a). This suggests that the front also acted as an ecotone between the coastal and offshore area, allowing the local mingling of OTUs from separated water masses. This ecotone was probably favored by the displacements of the front that allowed the mixing of water masses and communities from neighbor areas77. Although dispersal is a common feature of phytoplankton diversity patterns8 (especially across large12,78 or smaller oceanic fronts13,21), the existence of phytoplankton ecotones is seldom reported79. Two scenarios can be envisioned for the sustaining of an ecotone at the front: (1) OTUs (quiescent or growing) migrated recently in detectable proportions, or (2) OTUs have migrated earlier but have been sustained locally in detectable proportions. Both scenarios were evidenced, as the frontal station showed a higher OTU-connectivity: (1) within seasons, supposing recent migration, and (2) across seasons, supposing earlier migration of sustained OTUs (Fig. 4a; Supplementary Fig. S4). Water mixing was thus crucial in bringing together OTUs from separated areas, while the relaxation of selection favored the sustaining of OTUs over the front21.
Finally, by studying the patterns of rare and abundant phytoplankton OTUs in late summer, we evidenced that 50% of the diversity hotspot was made-up of OTUs specific to this station (Fig. 3b), most of which were shown to be rare (Fig. 3c). The maintaining of rare OTUs at the front contrasted with the shrinking of the rare phytoplankton richness across seasons (Fig. 3c). Hence, our approach seems to support the results of a recent theoretical study which hypothesize that reduction of competition in the vicinity of fronts mostly promotes rare protistan diversity80. Overall, the tidal front thus shaped a hotspot of eukaryotic phytoplankton diversity by mixing the abundant OTUs of neighboring areas and by lowering competitive exclusion, which sustained a higher number of rarer phytoplankton OTUs.
Hindsight from a trait approach
With a trait approach, we studied the ecological strategies that were selected in the Iroise Sea throughout summer. The principal goals were to test: (1) the existence of ecological strategies selected by the Ushant tidal front, and (2) if the hotspot of phytoplankton taxonomic diversity was also translated in a high richness of ecological strategies.
In September, after months of selection, the successful ecological strategies found at the front were not significantly distinct from those found in other areas (Fig. 7). This result invalidates the hypothesis that a coastal tidal front could select one or more specific strategies81, e.g. a strategy adapted to the variability of the front’s hydrographic features23,34. The lag between phytoplankton’s generation time (from one to a few days67,82) and the period of dominant disturbances at the front (14 days for the spring/neap cycle23,35) probably explains the lack of an emergent adapted strategy to the front.
The frontal area presented high phytoplankton taxonomic richness that did not translate into a higher functional richness by the end of summer (Fig. 6). This result supposes a high functional redundancy in the hotspot of diversity83. In a previous study of lake phytoplankton84, a decrease in competition also led to higher species richness with however a small variance in traits. The authors supposed that only a share of the present ecological strategies (or trait space in reference84) was affected by the decrease in competition. As a consequence, taxonomic richness was sustained only within these selected strategies leading to higher redundancy. However, we ruled this mechanism out, as the front did not appear to favor a specific strategy (Fig. 7). Our results are perhaps more reminiscent of a study on phytoplankton from coastal lagoons, where authors found that selection-induced competitive exclusion occurred primarily within functional groups85. Indeed, in areas other than the front all ecological strategies were present in similar proportions, but intra-strategy richness shrunk.
Our trait approach remains flawed by the lack of biological knowledge on most marine protists, which limits the number of OTUs and traits investigated, as well as the potential ecological interpretations43. As an example, it is impossible to rule out the fact that other types of ecological strategies (e.g. based on traits related to uptake or thermal preferences not included in our trait base) could be specific to the front43. Weighted functional metrics (weighting by the abundance or biomass of the taxa) are also likely to put more emphasis on the selected taxa which would likely yield distinct patterns of functional diversity83. In our non-weighted approach (due to the use of DNA-barcoding), the patterns of functional richness were indeed conditioned by the presence of Rhizarians, which represent a very distinct ecological strategy but were not among the most abundant taxa. We advocate for the development of further trait approaches in order to gain better insights on the interplay between phytoplankton and their ecosystem.
Using oceanographic measurements, DNA barcoding and a trait approach we detailed the setting of a eukaryotic phytoplankton diversity hotspot over a coastal tidal front. Our results reach a consensus with previous theoretical approaches concerning the combined effect of dispersal and selection processes on the sustaining of phytoplankton diversity at the meso- and submeso-scale14,18,19. We generalized and confirmed previous results from few phytoplankton taxa to the whole eukaryotic phytoplankton community21, and we detail how these processes seem to affect taxa differently according to their abundance. We detail processes leading to functional redundancy in the hotspot of phytoplankton diversity, however we cannot rule out that the frontal area selects species according to non-annotated traits, most notably traits involved in temperature and nutrient-based selection. Through its cascading effects on zooplankton, fish and fisheries23,86, this phytoplankton diversity hotspot is essential to the large and productive food-web of the Iroise Sea33,70,87. A higher frequency in the sampling of phytoplankton communities, a better approximation of the variables structuring them (e.g. light availability, grazing pressure) and further hindsight on the history of water masses are still required to calibrate models at the regional scale20. Understanding and predicting the interdependent relationship between oceanic processes and the organisms that depend on them remains challenging but crucial, especially in the face of climate change and its predicted impact on oceanic ecosystems.
Our sequencing dataset and associated metadata are available at: https://sextant.ifremer.fr/record/16bc16ef-588a-47e2-803e-03b4acb85dca/. The trait database of marine protist is accessible at: https://doi.org/10.17882/51662.
Falkowski, M. et al. Biogeochemical controls and feedbacks on ocean primary production. Science 281, 200–207 (1998).
Worden, A. Z. et al. Rethinking the marine carbon cycle: Factoring in the multifarious lifestyles of microbes. Science (80–) 347, 1257594 (2015).
Legendre, L. The significance of microalgal blooms for fisheries and for the export of particulate organic carbon in oceans. J. Plankton Res. 12, 681–699 (1990).
Brander, K. M. Global fish production and climate change. Proc. Natl. Acad. Sci. USA 104, 19709–19714 (2007).
Cardinale, B. J. Biodiversity improves water quality through niche partitioning. Nature 472, 86–89 (2011).
Striebel, M., Singer, G., Stibor, H. & Andersen, T. ‘Trophic overyielding’: Phytoplankton diversity promotes zooplankton productivity. Ecology 93, 2719–2727 (2012).
Irigoien, X., Huisman, J. & Harris, R. P. Global biodiversity patterns of marine phytoplankton and zooplankton. Nature 429, 863–867 (2004).
Chust, G., Irigoien, X., Chave, J. & Harris, R. P. Latitudinal phytoplankton distribution and the neutral theory of biodiversity. Glob. Ecol. Biogeogr. 22, 531–543 (2013).
Righetti, D., Vogt, M., Gruber, N., Psomas, A. & Zimmermann, N. E. Global pattern of phytoplankton diversity driven by temperature and environmental variability. Sci. Adv. 5, eaau6253 (2019).
Della Penna, A. & Gaube, P. Overview of (sub)mesoscale ocean dynamics for the NAAMES field program. Front. Mar. Sci. 6, 1–7 (2019).
d’Ovidio, F., De Monte, S., Alvain, S., Dandonneau, Y. & Levy, M. Fluid dynamical niches of phytoplankton types. Proc. Natl. Acad. Sci. 107, 18366–18370 (2010).
Villar, E. et al. Environmental characteristics of Agulhas rings affect interocean plankton transport. Science (80–) 348, 1261447–1261447 (2015).
Mousing, E. A., Richardson, K., Bendtsen, J., Cetinić, I. & Perry, M. J. Evidence of small-scale spatial structuring of phytoplankton alpha- and beta-diversity in the open ocean. J. Ecol. 104, 1682–1695 (2016).
Lévy, M., Franks, P. J. S. & Smith, K. S. The role of submesoscale currents in structuring marine ecosystems. Nat. Commun. 9, 4758 (2018).
Perruche, C., Rivière, P., Lapeyre, G., Carton, X. & Pondaven, P. Effects of surface quasi-geostrophic turbulence on phytoplankton competition and coexistence. J. Mar. Res. 69, 105–135 (2011).
Prairie, J. C., Sutherland, K. R., Nickols, K. J. & Kaltenberg, A. M. Biophysical interactions in the plankton: A cross-scale review. Limnol. Oceanogr. Fluids Environ. 2, 121–145 (2012).
Adjou, M., Bendtsen, J. & Richardson, K. Modeling the influence from ocean transport, mixing and grazing on phytoplankton diversity. Ecol. Modell. 225, 19–27 (2012).
Clayton, S., Dutkiewicz, S., Jahn, O. & Follows, M. J. Dispersal, eddies, and the diversity of marine phytoplankton. Limnol. Oceanogr. Fluids Environ. 3, 182–197 (2013).
Lévy, M., Jahn, O., Dutkiewicz, S., Follows, M. J. & d’Ovidio, F. The dynamical landscape of marine phytoplankton diversity. J. R. Soc. Interface 12, 20150481 (2015).
Cadier, M., Sourisseau, M., Gorgues, T., Edwards, C. A. & Memery, L. Assessing spatial and temporal variability of phytoplankton communities’ composition in the Iroise Sea ecosystem (Brittany, France): A 3D modeling approach: Part 2: Linking summer mesoscale distribution of phenotypic diversity to hydrodynamism. J. Mar. Syst. 169, 111–126 (2017).
Clayton, S., Lin, Y. C., Follows, M. J. & Worden, A. Z. Co-existence of distinct Ostreococcus ecotypes at an oceanic front. Limnol. Oceanogr. 62, 75–88 (2017).
Hill, A. E. et al. Thermohaline circulation of shallow tidal seas. Geophys. Res. Lett. 35, 5–9 (2008).
Sharples, J. et al. Internal tidal mixing as a control on continental margin ecosystems. Geophys. Res. Lett. 36, 1–5 (2009).
Franks, P. J. S. Phytoplankton blooms at fronts: Patterns, scales, and physical forcing mechanisms. Rev. Aquat. Sci. 6, 121–137 (1992).
Simpson, J. H. The shelf-sea fronts: Implications of their existence and behaviour. Philos. Trans. R. Soc. A 302, 531–546 (1981).
Le Fèvre, J., Viollier, M., Le Corre, P., Dupouy, C. & Grall, J. R. Remote sensing observations of biological material by LANDSAT along a tidal thermal front and their relevancy to the available field data. Estuar. Coast. Shelf Sci. 16, 37–50 (1983).
Sverdrup, H. U. On conditions for the vernal bloom of phytoplankton. J. Cons. Perm. Int. Explor. Mer 18, 287–295 (1953).
Morin, P., Le Corre, P. & Le Févre, J. Assimilation and regeneration of nutrients off the west coast of brittany. J. Mar. Biol. Assoc. United Kingdom 65, 677–695 (1985).
Cloern, J. E. Phytoplankton bloom dynamics in coastal ecosystems: A review with some general lessons from sustained investigation of San Francisco Bay, California. Rev. Geophys. 34, 127 (1996).
Simpson, J. H. & Hunter, J. R. Fronts in the Irish Sea. Nature 250, 404–406 (1974).
Mariette, V. & Le Cann, B. Simulation of the formation of Ushant thermal front. Cont. Shelf Res. 4, 20 (1985).
Sharples, J. et al. Spring-neap modulation of internal tide mixing and vertical nitrate fluxes at a shelf edge in summer. Limnol. Oceanogr. 52, 1735–1747 (2007).
Le Fèvre, J. Aspects of the biology of frontal systems. Adv. Mar. Biol. 23, 163–299 (1986).
Maguer, J. F., L’Helguen, S. & Waeles, M. Effects of mixing-induced irradiance fluctuations on nitrogen uptake in size-fractionated coastal phytoplankton communities. Estuar. Coast. Shelf Sci. 154, 1–11 (2015).
Cadier, M., Gorgues, T., LHelguen, S., Sourisseau, M. & Memery, L. Tidal cycle control of biogeochemical and ecological properties of a macrotidal ecosystem. Geophys. Res. Lett. 44, 8453–8462 (2017).
Sharples, J. Potential impacts of the spring-neap tidal cycle on shelf sea primary production. J. Plankton Res. 30, 183–197 (2008).
Zhou, J. & Ning, D. Stochastic community assembly: Does it matter in microbial ecology?. Microbiol. Mol. Biol. Rev. 81, 1–32 (2017).
Hardin, G. The exclusion competitive principle. Am. Assoc. Adv. Sci. 131, 1292–1297 (1960).
Barton, A. D., Dutkiewicz, S., Flierl, G., Bragg, J. & Follows, M. J. Patterns of Diversity in Marine Phytoplankton. Science (80–) 327, 1509–1512 (2010).
Charria, G. et al. Surface layer circulation derived from Lagrangian drifters in the Bay of Biscay. J. Mar. Syst. 109–110, S60–S76 (2013).
Ménesguen, A. et al. How to avoid eutrophication in coastal seas? A new approach to derive river-specific combined nitrate and phosphate maximum concentrations. Sci. Total Environ. 628–629, 400–414 (2018).
Litchman, E. & Klausmeier, C. A. Trait-based community ecology of phytoplankton. Annu. Rev. Ecol. Evol. Syst. 39, 615–639 (2008).
Ramond, P. et al. Coupling between taxonomic and functional diversity in protistan coastal communities. Environ. Microbiol. 21, 730–749 (2019).
Aminot, A. & Kérouel, R. Dosage Automatique des Nutriments Dans les Eaux Marines: Méthodes en Flux Continu. (2007).
Stoeck, T. et al. Multiple marker parallel tag environmental DNA sequencing reveals a highly complex eukaryotic community in marine anoxic water. Mol. Ecol. 19, 21–31 (2010).
Edgar, R. C., Haas, B. J., Clemente, J. C., Quince, C. & Knight, R. UCHIME improves sensitivity and speed of chimera detection. Bioinformatics 27, 2194–2200 (2011).
de Vargas, C. et al. Eukaryotic plankton diversity in the sunlit ocean. Science (80–) 348, 1261605 (2015).
Guillou, L. et al. The Protist Ribosomal Reference database (PR2): A catalog of unicellular eukaryote Small Sub-Unit rRNA sequences with curated taxonomy. Nucleic Acids Res. 41, 597–604 (2013).
Mahé, F., Rognes, T., Quince, C., de Vargas, C. & Dunthorn, M. Swarm v2: Highly-scalable and high-resolution amplicon clustering. PeerJ 1420, 1–20 (2015).
R Core Team. R: A Language and Environment for Statistical Computing. (2018). R version 3.5.0 (2018-04-23)---"Joy in Playing". www.r-project.org.
Mitra, A. The perfect beast. Sci. Am. 318, 26–33 (2018).
Oksanen, J. et al. vegan: Community Ecology Package. (2018).
Hsieh, T. C., Ma, K. H. & Chao, A. iNEXT: An R package for interpolation and extrapolation in measuring species diversity. 1–18 (2014). https://doi.org/10.1111/2041-210X.12613.
Csárdi, G. & Nepusz, T. The igraph software package for complex network research. J. Comput. Appl. https://doi.org/10.3724/SP.J.1087.2009.02191 (2014).
Stegen, J. C. et al. Quantifying community assembly processes and identifying features that impose them. ISME J. 7, 2069–2079 (2013).
Bruggeman, J. A phylogenetic approach to the estimation of phytoplankton traits. J. Phycol. 65, 52–65 (2011).
Callahan, B. J., Sankaran, K., Fukuyama, J. A., McMurdie, P. J. & Holmes, S. P. Bioconductor workflow for microbiome data analysis: From raw reads to community analyses [version 1; referees: 3 approved]. F1000Research 5, 1–49 (2016).
Kembel, S. W. et al. Picante: R tools for integrating phylogenies and ecology. Bioinformatics 26, 1463–1464 (2010).
Chase, J. M., Kraft, N. J. B., Smith, K. G., Vellend, M. & Inouye, B. D. Using null models to disentangle variation in community dissimilarity from variation in α-diversity. Ecosphere 2, 20 (2011).
Stegen, J. C., Lin, X., Fredrickson, J. K. & Konopka, A. E. Estimating and mapping ecological processes influencing microbial community assembly. Front. Microbiol. 6, 1–15 (2015).
Maire, E., Grenouillet, G., Brosse, S. & Villéger, S. How many dimensions are needed to accurately assess functional diversity? A pragmatic approach for assessing the quality of functional spaces. Glob. Ecol. Biogeogr. 24, 728–740 (2015).
Legendre, P. & Legendre, L. Numerical Ecology. Third English. (Elsevier, Oxford, 2012).
Massana, R. Eukaryotic picoplankton in surface oceans. Annu. Rev. Microbiol. 65, 91–110 (2011).
Litchman, E., Klausmeier, C. A., Schofield, O. M. & Falkowski, P. G. The role of functional traits and trade-offs in structuring phytoplankton communities: Scaling from cellular to ecosystem level. Ecol. Lett. 10, 1170–1181 (2007).
Margalef, R. Life-forms of phytoplankton as survival alternatives in an unstable environment. Oceanologia 1, 493–509 (1978).
Thingstad, T. F., Øvreas, L., Egge, J. K., Løvdal, T. & Heldal, M. Use of non-limiting substrates to increase size; a generic strategy to simultaneously optimize uptake and minimize predation in pelagic osmotrophs?. Ecol. Lett. 8, 675–682 (2005).
Marañón, E. Cell size as a key determinant of phytoplankton metabolism and community structure. Ann. Rev. Mar. Sci. 7, 241–264 (2015).
Raven, J. A. Small is beautiful: The picophytoplankton. Funct. Ecol. 12, 503–513 (1998).
Castaing, P. et al. Relationship between hydrology and seasonal distribution of suspended sediments on the continental shelf of the Bay of Biscay. Deep. Res. Part II Top. Stud. Oceanogr. 46, 1979–2001 (1999).
Schultes, S., Sourisseau, M., Le, E., Lunven, M. & Marié, L. Influence of physical forcing on mesozooplankton communities at the Ushant tidal front. J. Mar. Syst. 109–110, S191–S202 (2013).
Cabello, A. M., Latasa, M., Forn, I., Morán, X. A. G. & Massana, R. Vertical distribution of major photosynthetic picoeukaryotic groups in stratified marine waters. Environ. Microbiol. 18, 1578–1590 (2016).
Simo-Matchim, A.-G., Gosselin, M., Poulin, M., Ardyna, M. & Lessard, S. Summer and fall distribution of phytoplankton in relation to environmental variables in Labrador fjords, with special emphasis on Phaeocystis pouchetii. Mar. Ecol. Prog. Ser. 572, 19–42 (2017).
Vallina, S. M. et al. Global relationship between phytoplankton diversity and productivity in the ocean. Nat. Commun. 5, 4299 (2014).
Connell, J. Diversity in tropical rain forests and coral reefs. Science 199, 1302–1310 (1978).
Reynolds, C. S., Padisak, J. & Sommer, U. Intermediate disturbance in the ecology of phytoplankton and the maintenance of species diversity : A synthesis. Hydrobiologia 249, 183–188 (1993).
Fox, J. W. The intermediate disturbance hypothesis should be abandoned. Trends Ecol. Evol. 28, 86–92 (2013).
Chevallier, C. et al. Observations of the Ushant front displacements with MSG/SEVIRI derived sea surface temperature data. Remote Sens. Environ. 146, 3–10 (2014).
Raes, E. J. et al. Oceanographic boundaries constrain microbial diversity gradients in the South Pacific Ocean. Proc. Natl. Acad. Sci. https://doi.org/10.1073/pnas.1719335115 (2018).
Ribalet, F. et al. Unveiling a phytoplankton hotspot at a narrow boundary between coastal and offshore waters. Proc. Natl. Acad. Sci. 107, 16571–16576 (2010).
Villa Martín, P., Buček, A., Bourguignon, T. & Pigolotti, S. Ocean currents promote rare species diversity in protists. Sci. Adv. 6, eaaz9037 (2020).
Reynolds, C. S. Scales of disturbance and their role in plankton ecology. Hydrobiologia 249, 157–171 (1993).
Marañon, E. et al. Unimodal size scaling of phytoplankton growth and the size dependence of nutrient uptake and use. Ecol. Lett. 16, 371–379 (2013).
Mouillot, D., Gaham, N. A. J., Villéger, S., Mason, N. W. H. & Bellwood, D. R. A functional approach reveals community responses to disturbances. Trends Ecol. Evol. 28, 167–177 (2013).
Kruk, C. et al. Functional redundancy increases towards the tropics in lake phytoplankton. J. Plankton Res. 39, 518–530 (2017).
Leruste, A., Villéger, S., Malet, N., De Wit, R. & Bec, B. Complementarity of the multidimensional functional and the taxonomic approaches to study phytoplankton communities in three Mediterranean coastal lagoons of different trophic status. Hydrobiologia https://doi.org/10.1007/s10750-018-3565-4 (2018).
Pauly, D. & Christensen, V. Primary production required to sustain global fisheries. Nature 374, 255–257 (1995).
Ayata, S. D., Stolba, R., Comtet, T. & Thiébaut, E. Meroplankton distribution and its relationship to coastal mesoscale hydrological structure in the northern Bay of Biscay (NE Atlantic). J. Plankton Res. 33, 1193–1211 (2011).
This work was financed by the French Government under the programme ‘Investissements d’Avenir: Oceanomics (Grant ANR-11-BTBR-0008), by the project of the initiative Ecosphere Continentale et COtière (EC2CO) of the Institut National des Sciences de l’Univers/Centre National de la Recherche Scientifique (INSU/CNRS): POHEM (2016). This research was carried out within the framework of Pierre Ramond’s PhD, co-funded by Ifremer and Region Bretagne (Allocation de REcherche Doctorale (ARED) fellowship). We thank all members of the M2BIPAT consortia, as wells as the cruise members who contributed to samples’ collection with the Albert Lucas vessel from the French Oceanographic fleet. We also thank the Genotoul platform for samples’ sequencing (https://www.genotoul.fr/).
The authors declare no competing interests.
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Ramond, P., Siano, R., Schmitt, S. et al. Phytoplankton taxonomic and functional diversity patterns across a coastal tidal front. Sci Rep 11, 2682 (2021). https://doi.org/10.1038/s41598-021-82071-0