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Spatial distribution pattern of Mytilus chilensis beds in the Reloncaví fjord: hypothesis on associated processes



Natural M. chilensis populations dominate habitats with a steep environmental gradient, and that are characterized by abrupt changes in salinity and exposure to desiccation. Although these populations are the source of seed supplies for the Chilean mussel culture industry (annual production around 250 thousand Tons), knowledge about natural populations is scarce. Based on video transect recordings, this study carries out research into one of the principal mussel beds and its associated epibenthic community in the Reloncaví Fjord, both along cross-shore and along-shore distribution gradients.


Mytiluschilensis was observed between the middle intertidal zone and the upper subtidal zone (between approximately 9 and 26 psu), with a richer associated community towards the subtidal zone and the fjord mouth. The mussel Condition Index (total meat weight/shell length*100) in the intertidal zone was significantly greater than in the subtidal zone, which raises questions about the reproductive contribution of mussels along the intertidal mid-subtidal gradient.


Salinity and tidal variations, together with biological interactions, would seem to be key factors for explaining M. chilensis spatial distribution in the Reloncaví fjord, where beds appear to be in a contraction stage, as evidenced by M. chilensis scarcity towards the subtidal zone. The importance of these populations and their persistence in environments with high perturbation frequency, suggests a monitoring program should be implemented that considers both population spatial distribution and the changing environmental conditions.


The mussel Mytilus chilensis is a bivalve that forms dense beds on hard and muddy substrates up to a depth of 10 m, although, exceptionally, it has been observed at depths of up to 25 m (Lorenzen, et al. 1979; Zagal, et al. 2001). This species has separate sexes and a complex life cycle that alternates between a planktonic larval phase and a benthic adult phase (Buzeta, et al. 1988; Chaparro and Winter 1983). This gives rise to adult populations that are spatially structured in subpopulations according to habitat type and interconnected by means of larval dispersion (e.g., Hanski and Gilpin 1991; Roughgarden, et al. 1985).

Orensanz, et al. (1991), Orensanz and Jamieson (1998), and Orensanz, et al. (2006) proposed that analysis of the spatial dimension of population processes requires the identification of meaningful scales and adopted five scales for this purpose (Megascale, Macroscale, Mesoscale, Microscale, and Nanoscale). We will concentrate on the Mesoscale, corresponding to populations or subpopulations within a metapopulation, typically the scale of fishing grounds and beds (Orensanz et al. 1998). The dynamics of these subpopulations can be observed through their contraction and expansion, largely mediated by larval advection and habitat availability. These subpopulations may persist, become extinct, and re-emerge over periods of time that span more than a generation and changes can be slow and erratic (e.g., Caddy 1989; Hunt and Scheibling 2001).

Mytilus chilensis geographic distribution extends throughout the entire Chilean coastline and part of the Argentinean coast, dominating littoral communities in the fjords and channels of southern Chile that are characterized by marked salinity variations (Lorenzen, et al. 1979; Viviani 1979). These salinity variations give rise to a stratified system (Pickard 1971; Silva, et al. 1995; Valle-Levinson, et al. 2007), where it is assumed that vertical salinity gradients determine the spatial structure of the M. chilensis populations. This would occur mainly due to i) an effect on the planktonic phase, whereby the halocline functions as a chemical or physical barrier to those larvae attempting to migrate along these gradients (Gallager, et al. 2004; Lougee, et al. 2002; Young 1995) or ii) an effect on the survival of recruits and adults in a relatively variable environment.

Although Chilean mussel aquaculture activities harvest around 250,000 tons annually (Sernapesca 2013) and 99% of juveniles are obtained by recruitment on artificial substrates located in areas surrounding natural banks, knowledge regarding basic ecological aspects of natural populations is scarce. The only information available relates to a few isolated aspects regarding estimated abundance in some areas (Leiva, et al. 2007; Lizama 2003) and some knowledge about larval stages present in the water column (Avendaño, et al. 2011; Barría, et al. 2012).

In coincidence with the growth in mussel culture activities, recruitment on the artificial substrates decreased in traditional collection areas (Avendaño et al. 2011). From the 1990s onwards, these were replaced by other recruitment areas, towards the fjords of the Los Lagos region (Leiva et al. 2007). However, from 2010 to date, M. chilensis recruitment on artificial substrates has decreased in the Reloncaví fjord, one of the main recruitment zones. As well as threatening the Chilean mussel culture industry, this situation raises basic issues that require clarification: i) Are the M. chilensis populations in the Reloncaví fjord contracting or expanding?; ii) What are the processes regulating M. chilensis population dynamics in fjord and estuarine systems?; iii) Can the decrease in M. chilensis recruitment in the Reloncaví fjord be explained by the decline in abundance of natural beds of this species?

The aim of this study is to describe the spatial distribution pattern of M. chilensis in the Reloncaví fjord, as well as its associated community and environmental variables. Using these results, we discuss some of the processes which may regulate the population dynamics of this species, their effects on recruitment in natural beds and seed collection, and the consequences for the mussel aquaculture industry.


This research work studies the spatial distribution of M. chilensis and its associated community along a shallow bathymetric gradient in the Reloncaví fjord. Given the spatial distribution of mussels previously observed in the study area, it was considered necessary to use the classification reported by Lizama (2003) (included as Additional file 1) to distinguish the two types of mussels observed along the cross-shore distribution: M. chilensis covered by the barnacle Elminius kingii (hereafter referred to as ‘covered’) in the middle intertidal zone, and the mussels with little or no epibiont presence (hereafter referred to as ‘clean’) in the subtidal zone.

The M. chilensis condition index (total meat weight/shell length × 100) was characterized monthly from September 2013 to May 2014. Additionally, we studied food supply, expressed as phytoplanktonic biomass, as well as temperature and salinity in the water column.

Study area

The study area focused on the Reloncaví fjord that has a depth of just over 450 m and three moraine banks: at the head, in the middle, and at the mouth of the fjord. The tidal ranges in the fjord are 6 to 7 m during spring tides and 5 to 6 m during neap tides (Valle-Levinson et al. 2007), with greater tidal heights towards the mouth (50 cm) than at the head. Considering these features, Daneri, et al. (2009) proposed the division of the fjord into four zones (Boca, Marimelli, Puelo, and Cochamó) and we use this division to study the mussel’s beds in the fjord. The selection of specific sampling stations was based on previous work by Lizama (2003) in order to have a reference with which to compare results, considering the limited literature available on mussel beds in Chile. Specifically, 13 of the 22 sites sampled by Lizama (2003) along the fjord (Figure 1) were studied along cross-shore gradients, in vertical profiles of approximately 15 m between the high tide line (0 m) and the subtidal zone.

Figure 1
figure 1

A) Study area in southern Chile. B) Reloncaví fjord, where the divisions proposed by Daneri et al. (2009) are identified. The cross indicates monthly CI and phytoplanktonic biomass sampling sites. White circles indicate the sites sampled by Lizama (2003); circles with a black dot indicate sites sampled in 2013.

The M. chilensis condition index and environmental variables were obtained monthly in three sites representing the Boca, Marimelli, and Puelo zones. Cochamó was excluded from monthly surveys due to the elevated costs of this sampling activity.

Characterization of M. chilensis populations and associated community

The epibenthic species (>10-mm size) in the 13 sampling stations were characterized by recording five video transects, 20- to 26-m length (separated by 50 to 140 m), perpendicular to the coast line (cross-shore). In order to record the video transect, a Seaviewer camera (mounted on a sled) was towed from a depth of 12 to 15 m, to the surface. The sled was maintained more or less perpendicular at 35 cm from the bed and accompanied by a shellfish diver, who, in turn, indicated the onset of M. chilensis presence, which coincided with the end of the Aulacomya atra (ribbed mussel) presence. The camera was equipped with two lasers parallel to its line of vision, separated by a 10-cm-wide interval; this enabled estimation of width of the visual field and, finally, made it possible to obtain a qualitative classification of the organism size.

The position of the sled was monitored at 1-s intervals, using a Micron Nav USLB tracking system, mounted on the sled, enabling confirmation of transect demarcation and verification of the bathymetric profile associated with each video transect. In each transect, mussel samples were collected from the intertidal and subtidal level; to this end, a 25 × 25 cm quadrant was set up, and all mussels present within the quadrant were removed. All the mussels collected were counted and their valve length measured using a vernier caliper (1-mm accuracy).

Condition index and environmental variables

Thirty covered mussels (from the middle intertidal zone) and 30 clean mussels (from the subtidal zone) of between 50- and 70-mm length were collected at monthly intervals in three sites of the fjord (representing the Boca, Marimelli, and Puelo zones, Figure 1). Total length and drained wet weight of meat were obtained from these specimens. Length of each specimen was recorded using a vernier caliper accurate to ±1 mm. The meat weight of each specimen was obtained by weighing on an electronic precision scale ± 0.01 gr.

Mussel condition index (CI) was estimated as \( \mathrm{C}\mathrm{I}\kern0.5em =\frac{\mathrm{PT}}{\mathrm{LT}}\kern0.5em \times 100, \) where TW is total meat weight in grams and TL is total shell length in millimeters (Anderson and Neumann 1996).

Simultaneously, integrated water samples were collected in two strata, 0- to 5-m and 15- to 10-m depth, using a hose, 20-m length and 2.5-cm diameter, to determine chlorophyll in the water column. Two hundred milliliters of water was filtered at a pressure below 100 psi, using fiberglass filters (GF-75 MFS, 25-mm diameter). Estimation of autotrophic biomass measured as chlorophyll-a (μg L-1) was undertaken using the fluorometric method (Turner fluorometer). Temperature and salinity profiles were registered with a Seabird19 plus profiler. These were processed using the software provided by the manufacturer.

Video-transect processing

The images were projected onto the computer screen on a grid of 100 separate points, where the taxonomic groups were identified to the most specific level possible, depending on the image quality, according to Häuseermann and Försterra (2009). The sample comprises a frame identified by recording time (hh:mm:ss), where the image is frozen in order to identify and count all the taxonomic groups observed, estimate algal coverage, and identify substrate type. Each of the frames sampled was georeferenced using Micron Nav USBL tracking system information (obtaining the x, y, and z coordinates referring to the position of vessel). This enabled elaboration of distribution profiles for the main species observed, with a 1-m resolution.

Statistical analysis

M. chilensis spatial distribution was evaluated by applying geostatistical methods, following Roa-Ureta and Nicklitschek (2007), to adjust two independent models: a binomial model for the presence/absence data and a Gauss model for the positive density observations (box-cox transformed). Thus, two separate spatial correlation processes were evaluated. The first model evaluated whether there was spatial correlation in mussel distribution (presence/absence) in the area. The second model evaluated whether the positive observations were spatially correlated by means of the subset frames/video, where M. chilensis was present. The statistical significance of the spatial correlation was evaluated, based on a comparison of likelihood of the spatial model against an equivalent non-spatial model (pure nugget). Selection of the best model was undertaken using the Akaike information criterion (AIC) (Akaike 1974), where the preferred model presented the minimum AIC value, considering a ≥2 unit difference (Burnham and Anderson 2004).

The size distribution of sampled mussels was assessed relative to zone and strata (intertidal and subtidal) using regression models for ordinal data (McCullagh 1980) and the ordinal package in R 3.0.2 (Christensen 2012). To this end, mussel length distribution was separated into six intervals of 15 mm each. We evaluated six possible hypotheses as shown in Table 1.

Table 1 Hypothesis used for the comparative analysis of M. chilensis size distribution in four bathymetric zones and two strata

Monthly CI and chlorophyll-a variation was evaluated through the application of a linear model that considered the predictor variables: zone, stratum (as a fixed effect), and month (as a random variable), using the nlme package (Pinheiro et al. 2013). The residuals of both models were previously transformed with a box-cox function using the car package (Fox and Sanford 2010) in R 3.0.2 (The R Development Core Team 2013). Additionally, CI was evaluated through the application of a linear model that considered the predictor variables: temperature, salinity, and chlorophyll-a.

Variation in number of species and abundance per species for each sample zone was evaluated by means of non-metric multidimensional scaling; a Bray-Curtis similarity matrix was constructed, and Analysis of Similarities (ANOSIM) with 999 permutations was undertaken. A Similarity Percentage (SIMPER) analysis of species representatively among zones was also carried out, using PRIMER-E 5.0. ANOSIM generates an R statistic that varies between 0 and 1. The value R = 1 represents the absolute value of similarity, while R = 0 represents absolute dissimilarity among groups. The R value observed is contrasted with the R value obtained from the 999 permutations undertaken. If the similarity percentage within each group is less than that between groups R 0, then groups will be significantly similar (P ≥ 0.05). The species responsible for the differences observed between zones were identified by means of Similarity Percentage (SIMPER) analysis.


Characterization of M. chilensis beds and associated community

We identified 42 epibenthic taxonomic groups in the 13 sampling stations, with a predominance of the mussels M. chilensis and Aulacomya atra, the crustacean Elminius kingii, and species of Echinodermata (Tables 2 and 3, Additional file 2). Highest taxon richness was observed in the mouth of the fjord (21 to 28 species), while lowest taxon richness and abundance of individuals was observed at the head of the fjord in Cochamó (five to nine species) (Figure 2). Among the four zones studied, significant differences in taxa similarity were only observed between the Boca zone and the other zones (Table 2). Mainly, Gastropoda, Echinodermata, Mitilidae, and Crustacea were observed in the Boca zone of the fjord whereas, towards the head of the fjord (Cochamó), E. kingii and the mussels A. atra and M. chilensis dominated (Table 3).

Table 2 Result of a non-metric multidimensional scaling that compares the four sampling zones
Table 3 Results of non-metric multidimensional scaling for taxa diversity in four zones of the Reloncaví fjord
Figure 2
figure 2

Number of taxa of epibenthic groups recorded in the 13 sampling sites of the Reloncaví fjord.

Mytilus chilensis distribution was observed between the middle intertidal and upper subtidal zone in 12 of the 13 stations sampled (between approximately 2 and 12 m in our vertical profile (Figure 3)). Covered M. chilensis were observed in the intertidal zone (maximum density = 1,100 Ind/m2); while in the subtidal zone, the mussels were mainly clean (maximum density = 350 Ind/m2). Mussel distribution increased in depth towards the head of the fjord (Figure 3), in coincidence with the accentuation of a salinity gradient between 8 and 26 psu. Ribbed mussel was observed between 6 and 13 m of the vertical profile (subtidal), with the exception of the Cochamó zone. Highest ribbed mussel density (maximum density = 900 Ind/m2) was observed in the Marimelli and Puelo zones (Figure 3). Echinodermata, represented mainly by Asteroidea, Loxechinus albus, and Arbacia dufresnei, were observed principally in the Boca zone, between approximately 8 and 14 m (Figure 3).

Figure 3
figure 3

Average density of four taxa representative of the epibenthic community. The epibenthic community of organisms that inhabits the area from the intertidal zone to a depth of 15 m, in 13 sampling sites in the Reloncaví fjord. Centered symbol referring to depth, represents a range of between 0 to 400 Ind/m2. Grey-shaded area shows the position of a halocline between 8 and 26 psu during the sampling period. Black vertical lines indicate the limits between sampling zones.

Throughout the sampling, salinity between 0 and 15 m presented a gradient ranging from 5 to 30 psu, which, at the mouth of the fjord, included an area from the surface to over 10-m depth; whereas, at the head of the fjord, it ranged from the surface to over 15-m depth. The most pronounced salinity gradient was observed between approximately 8 and 26 psu, shaded in grey in Figure 3.

Geostatistical analysis revealed evidence of spatial correlation in the distribution of mussels (presence/absence) in 83% of cases (AIC spatial model to AIC non-spatial model >2), with a range of spatial proximity that varied between 2 and 24 m and an average range of 6.8 m. Evidence of spatial correlation in M. chilensis density was only observed in two sites, with a range of 4 and 8 m (Table 4). These results suggest that we observed the effect of spatial proximity in mussels, but we did not observe spatial dependence on mussel density. Our results could be affected by the sampling design used and the narrow belt of mussels (transects perpendicular to the coastline), since other authors found that the distribution of adult mussels showed spatial dependence along transects of 10 m (see Erlandsson and McQuaid 2004).

Table 4 Results of geostatistic analysis following Roa-Ureta and Niklitschek ( 2007 )

Size distribution of covered M. chilensis was symmetric towards the mouth of the fjord, while towards the head, size distribution showed a bias towards larger individuals (Figure 4). Clean mussels were only found in the Boca and Puelo zones (Figure 4), presenting a biased size distribution towards mussels measuring 40- to 80-mm length. The ordinal model applied showed that the full model (difference between stratum and zones) was the most informative of the six models assessed (AIC = 12,052), with regard to explaining the size distribution of mussels along the Reloncaví fjord (Table 5).

Figure 4
figure 4

Size distribution of M. chilensis covered with E. kingii (covered) and without epibionts (clean). In four sampling zones of the Reloncaví fjord. n indicates number of mussels in the sample.

Table 5 Evaluation of the size distribution of mussels from zones and depth stratum (intertidal and subtidal)

Condition index and environmental variables

The M. chilensis condition index was significantly greater towards the mouth of the fjord (F2,1525 = 158.91; P = 0.0001), with values over 90% and reaching up to 230%, during the study period, while at the Puelo site, CI remained at around 90% (Table 6, see also Figure S1 in Additional file 2). In turn, significant differences in CI were observed between strata (F2, 1525 = 158.91; P = 0.0001), with greater CI between 0- and 5-m depth (Table 6, see also Figure S2 in Additional file 2). The condition index showed no significant variations due to the changes in chlorophyll-a concentration, salinity, or temperature during the study period.

Table 6 Statistical significance of variation in M. chilensis condition index

Phytoplanktonic biomass varied between 0.5 and 9 μg chlorophyll-a L−1 throughout the entire study period, with higher values in September 2014. Significant differences were only observed in the phytoplanktonic biomass between the Marimelli and Puelo zones, with greater phytoplanktonic biomass in the latter site (F2,133 = 4.07; P = 0.0192) (Table 7, see also Figure S2 in Additional file 2). No significant differences were observed between the two strata studied (F2,133 = 2.72; P = 0.1013) (Table 7).

Table 7 Statistical significance of variation in phytoplanktonic biomass

The water column remained stratified during the sampling periods, with a shallower halocline towards the mouth of the fjord and during the summer months. Salinity varied between approximately 8 psu on the surface and 32 psu at 15-m depth. Thermocline was greatest between November and January, with maximum values of 20°C on the surface and 11°C to 12°C at 15-m depth (Figure 5).

Figure 5
figure 5

Temperature contours (°C) and salinity (psu) of the water column. Temperature contours (°C) (A, C, E) and salinity (psu) (B, D, F) of the water column between 0- and 15-m depth in Boca (A, B), Marimelli (C, D), and Puelo (E, F).


As reported by Viviani (1979), M. chilensis was observed in narrow ‘belts’ of approximately 6 m wide in the Reloncaví fjord, in a habitat characterized by the presence of a steep salinity gradient between approximately 9 and 26 psu (see also Daneri et al. 2009). In turn, the taxa composition presented a gradient from the mouth towards the head of the fjord, associated with the deepening of the halocline. This suggests that salinity gradient plays an important role in structuring the community associated with M. chilensis, where this species is confined to a narrow habitat that is bordered by physical-chemical restrictions towards the upper boundary (Aquaterra Ingenieros Ltda. 2010; Buschbaum, et al. 2009). Towards the inferior zone of its distribution, M. chilensis seems to compete for substrate with A. atra, which has only been observed on culture ropes where the two species recruit together (Marambio, et al. 2012). Both the urchins A. dufresnii and starfish observed in our study are carnivorous and therefore may be predators of A. atra and M. chilensis (Brogger, et al. 2010; Häuseermann and Försterra 2009; Zaixso 2004). However, it is likely that the salinity gradient in the water column restricts the periods in which these predators have access to these prey in stratified environments.

The structure of the intertidal and shallow subtidal communities in rocky systems has been described and discussed in scientific literature (Connell 1961; Hunt and Scheibling 2001; Paine 1974; Reusch and Chapman 1997). These authors proposed the presence of intra- and interspecific competition between organisms that adhere to the substrate, as well as predation, for example, by Echinodermata. The limited information available on intertidal ecology in Chilean fjords and channels restricts the understanding of patterns observed. Considering the demand for use of these coastal areas (e.g., for aquaculture, fisheries, tourism, etc., see Molinet, et al. 2014), research into coastal ecology must be undertaken in order to provide the necessary knowledge to ensure that the correct decisions are taken in the context of sustainable development.

The size distribution of M. chilensis showed significant differences between the intertidal and subtidal zones and among the four areas studied, suggesting a local pattern of size distribution with a low number of recruits at the head of the fjord. Erlandsson and McQuaid (2004) observed that the distribution of larger recruits of Perna perna showed spatial dependence at 10-m transects, revealing a spatial structure related to that of adults. Furthermore, the size distribution pattern of area-specific mussels are influenced by their mortality and growth rates due to local conditions, as observed by McQuaid and Lindsay (2000) for the mussel P. perna in exposed and sheltered environments. Thus, studying variations in mortality and growth rates associated with the salinity gradient affecting the mussel bed and how they are expressed in the size distribution pattern observed will contribute to understanding the population dynamics of M. chilensis in stratified systems, such as the Reloncaví fjord.

The steep saline gradient observed between 3 and 10 m of the water column appears to modulate the marked changes in M. chilensis abundance, as well as characteristics such as valve cover ranging from mussels completely covered by E. kingii in the intertidal zone to totally clean mussels in the subtidal zone. Along this gradient, those individuals in the intertidal zone (covered) present a better CI than the clean individuals, throughout this study. Additionally, mussel CI decreases significantly towards the head of the fjord, which may be associated, principally, with effects of the deepening halocline, food availability, and environmental stress. The latter has been reported to affect the gonadic index in the case of Mytilus californianus and, therefore, their contribution to reproduction (Petes et al. 2008).

Observations undertaken in our study raise new questions with regard to the spatial distribution pattern of M. chilensis and the differences in its condition index on a scale of meters. Our hypothesis is that the environmental gradient observed in this narrow belt configures a ‘source-sink’ habitat scenario (sensu Pulliam 1988) for M. chilensis that requires further in-depth study. The existence of a source-sink habitat for M. chilensis in the spatial scale observed would imply that, along this narrow and highly perturbed gradient, part of the population does not contribute (or contributes little) to population growth.

On the other hand, the scarcity of clean mussels and lower densities of covered mussels observed in our study, compared to the observations of Lizama (2003) (see Figure S3 Additional file 1), suggest a narrowing of the space occupied by the mussel belt and a decrease in the abundance of M. chilensis in the Reloncaví fjord. Unfortunately, we found no previous information regarding mussel belt width or the role that covered mussels (in the intertidal) and clean mussels (in the subtidal) may have; thus, it is suggested that these aspects be included in future studies.

One approach to studying changes in the abundance of mussel belts could be the contraction/expansion dynamics of subpopulations (e.g., Orensanz et al. 1998; Orensanz et al. 2006). Hunt and Scheibling (2001) described aspects of the expansion and contraction of mussel beds, indicating that they can recover over a relatively short period of time. In particular, we suggest studying changes in the cross-shore spatial distribution and abundance of mussels and their relationship with changes in water column salinity, rain, and rain runoff.

Thus, the cross-shore contraction-expansion dynamics of mussel beds appear to be an effective instrument for monitoring these spatially structured populations; it considers a spatial scale that allows us to observe annual changes, which in turn may be related to environmental variations such as the pycnocline depth and discharge rainwater. Additionally, geostatistical analysis techniques could also be included (e.g., Roa-Ureta and Niklitschek 2007) to enable characterization of the spatial distribution pattern of this species.

Contraction of the M. chilensis beds in the Reloncaví fjord may be associated with i) environmental instability (and the consequent natural deficiencies in recruitment), ii) the removal of recruits as a result of an indeterminate number of artificial substrata (seed collectors) installed and removed annually from the system (Leiva et al. 2007), iii) the exploitation of natural beds (Sernapesca 2013), and iv) predation, among other factors.

These elements, together with the prevailing environmental conditions in the fjord, may be creating scenarios that lead to increased variability in the reproductive success of M. chilensis; given the ecological, social, and economic importance of this species along the Chilean coast, the establishment of a monitoring program that considers these factors is imperative.


Ours results suggest that salinity gradient plays an important role in structuring the community associated with M. chilensis, where this species is confined to a narrow habitat that is bordered by physical-chemical restrictions towards the upper boundary. It is also influencing the size distribution of M. chilensis, which showed significant differences between the intertidal and subtidal zones and along the fjord, suggesting a local pattern of size distribution with a low number of recruits at the head of the fjord.

The scarcity of clean mussels and lower densities of covered mussels observed in our study, compared to the observations of previous works suggest a narrowing of the space occupied by the mussel belt and a decrease in the abundance of M. chilensis in the Reloncaví fjord. One approach to studying changes in the abundance of mussel belts could be the contraction/expansion dynamics of subpopulations in the cross-shore spatial distribution of mussels and their relationship with changes in water column salinity, rain, and rain runoff. Contraction of the M. chilensis beds in the Reloncaví fjord may be associated with i) environmental instability, ii) the removal of recruits as a result of an indeterminate number of artificial substrata (seed collectors) installed and removed annually from the system, iii) the exploitation of natural beds and iv) predation, among other factors. These elements may be creating scenarios that lead to increased variability in the reproductive success of M. chilensis and therefore threaten the seeds supply from natural environments for mussel aquaculture.


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This study was financed by FONDECYT Project No. 1130716. The collaboration of César Arre Krause, Captain of the L/M Jürgen Winter, César Arre Reyes, and Camilo Almonacid is much appreciated. The authors also thank Susan Angus for the translation of the manuscript and two anonymous reviewers who contributed to improving this article.

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Correspondence to Carlos Alberto Molinet Flores.

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The authors declare that they have no competing interests.

Authors’ contributions

CM carried out in the sample design, participated in sampling, data analysis and drafted the manuscript. MD participated in sampling and data analysis. CA participated in sampling, data analysis. LC participated in sampling drafted the manuscript. SM participated in drafted the manuscript. MA participated in drafted the manuscript. EN participated in drafted the manuscript and data analysis. All authors read and approved the final manuscript.

Additional files

Additional file 1: Table S1.

Taxa found along 13 sampling stations between 0 and 15 m (from the upper tidal level) in the Reloncaví fjord.

Additional file 2:

Catastro de bancos naturales de mitilidos en el estuario reloncaví.

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Flores, C.A.M., Gomez, M.A.D., Muñoz, C.B.A. et al. Spatial distribution pattern of Mytilus chilensis beds in the Reloncaví fjord: hypothesis on associated processes. Rev. Chil. de Hist. Nat. 88, 11 (2015).

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