Skip to main content

Thank you for visiting You are using a browser version with limited support for CSS. To obtain the best experience, we recommend you use a more up to date browser (or turn off compatibility mode in Internet Explorer). In the meantime, to ensure continued support, we are displaying the site without styles and JavaScript.

Tracking a mass mortality outbreak of pen shell Pinna nobilis populations: A collaborative effort of scientists and citizens


A mass mortality event is devastating the populations of the endemic bivalve Pinna nobilis in the Mediterranean Sea from early autumn 2016. A newly described Haplosporidian endoparasite (Haplosporidium pinnae) is the most probable cause of this ecological catastrophe placing one of the largest bivalves of the world on the brink of extinction. As a pivotal step towards Pinna nobilis conservation, this contribution combines scientists and citizens’ data to address the fast- and vast-dispersion and prevalence outbreaks of the pathogen. Therefore, the potential role of currents on parasite expansion was addressed by means of drift simulations of virtual particles in a high-resolution regional currents model. A generalized additive model was implemented to test if environmental factors could modulate the infection of Pinna nobilis populations. The results strongly suggest that the parasite has probably dispersed regionally by surface currents, and that the disease expression seems to be closely related to temperatures above 13.5 °C and to a salinity range between 36.5–39.7 psu. The most likely spread of the disease along the Mediterranean basin associated with scattered survival spots and very few survivors (potentially resistant individuals), point to a challenging scenario for conservation of the emblematic Pinna nobilis, which will require fast and strategic management measures and should make use of the essential role citizen science projects can play.


The pen shell Pinna nobilis (Linnaeus, 1758), is the largest bivalve of the Mediterranean Sea where it is endemic; and with its size of up to 1.2 m height ranks as one of the largest worldwide1,2,3. This species grows on soft-bottom coastal areas and mainly inhabits seagrass meadows (dominated by Posidonia oceanica and Cymodocea nodosa), but also occasionally thrives on unvegetated bottoms, maërl beds, or among boulders2,4,5,6. In favourable conditions the lifespan of P. nobilis is up to 50 years7 and the species develops a key ecological role. Pen shells filter water and retain large amounts of organic matter from suspended detritus8, contributing to water clarity. In addition, its shell provides a hard-surface within a soft-bottom ecosystem, which is colonized by many different benthic species9,10,11, and at high densities can create high-diversity biogenic reefs12. It also plays a key role in the trophic web, serving as prey of other species (e.g., Octopus vulgaris13,14) and host of symbionts like the crustaceans Pontonia pinnophylax and Nepinnotheres pinnotheres15.

Several anthropogenic pressures such as pollution16,17, anchoring18,19, harvesting20, habitat degradation21,22 and environmental threats like for example global warming, which induces a decrease in juveniles’ survival rate23 have contributed to accelerate the decline of pen shell populations in the last century, making this emblematic species one of the most important bio-indicators of ecosystem status in the Mediterranean basin. This decline has in turn led to list the pen shell as an endangered and protected species under Annex IV of the Habitats Directive (European Council Directive 92/43/EEC), Annex II of the Barcelona Convention, and national legislation in most Mediterranean countries.

Recently, pen shell’s population health in Spain has plummeted, causing concern and a status change from “Vulnerable” category to “Critically Endangered” with a serious extinction risk (Orden TEC/1078/2018). This is due to a Mass Mortality Event (MME24,25) that affected P. nobilis populations of the south-western Mediterranean Sea starting in early autumn 2016 with extremely high mortality levels (reaching up to 100% at monitored populations26). Thereafter, severe mortality was also observed in pen shell populations from the north-western Mediterranean (Italian and French coasts27) and as far as the Aegean sea28. As in two regions of Italy (Campania and Sicily) a mycobacterial disease has recently been associated with the mortality episodes of P. nobilis29, the role of a Mycobacterium sp. in a complex disease pathogenesis cannot be discarded. However, also in Italy30 there is compelling evidence that the main cause of this mortality wave is the protozoan Haplosporidium pinnae, a new species genetically related to the group of Haplosporidian parasites27. Different life stages of this parasite have been detected in diagnosed sick pen shells. The sporulation stage of the protozoa has been detected in the digestive gland, while the uninucleate and the less frequent plasmodial stages have been found in the connective tissue and the gut epithelium. This type of infection triggers a heavy inflammatory response with harmful physiological responses for the host (e.g., precluding the digestion process), finally causing the death of the animal27,31.

Haplosporidian endoparasites have been the cause of mortality events in other bivalve populations. They have been specifically well-studied in cases of molluscs of commercial interest, most likely due to the socio-economic repercussions. The best studied members of the group are Haplosporidium nelsoni and Bonamia ostreae which cause die-backs in the oysters Crassostrea virginica (Atlantic coasts of USA32,33) and Ostrea edulis (European coasts34,35), respectively. Several studies suggest a key role of the environment affecting the life-cycle of these parasites32,36,37. The disease prevalence and intensity shows seasonal patterns; for example, a peak of prevalence at higher summer temperatures and salinity was observed for H. nelsoni38,39 and Bonamia exitiosa40,41. While B. ostreae shows the same pattern for salinity (prevalence decreases at lower salinities), in contrast, the parasite outside its host showed higher survival and esterase activities at 4 °C and 15 °C than at 25 °C42,43. Little is known about the environmental dispersal of Haplosporidians although oceanic currents have been suggested as a potential factor driving the expansion of these parasites42,44. The quick northward expansion of the disease along the Iberian peninsula during the present outbreak26, with early outbreaks in the Central Mediterranean28, agrees with the hypothesis of a pivotal role of currents in disease dispersal at regional but also basin-wide scales. The occurrence of healthy P. nobilis populations in specific areas (e.g., Alfacs Bay in the Ebro Delta, with low salinity caused by freshwater discharges) points towards a relation between environmental factors such as salinity and/or temperature on disease prevalence or survival of H. pinnae.

However, the study of rapid and vast pathogen dispersal (e.g., invasive diseases) as well as the relationship with environmental parameters is often constrained by the scale45 and time-period needed for observations. The problem of intense sampling effort can be resolved with networks of citizen and scientists, which can multiply the spatio-temporal sampling effort without the economic and logistic constraints of scientific sampling46. Here, we have combined observations of scientists and citizens to track the mass mortality outbreak caused by the new species-specific parasite H. pinnae27 in order to test if dispersal speed is coherent with local current patterns and to investigate if there are environmental factors aiding the infection of pen shell populations by the pathogen. This could provide an indication of further future dispersal of the pathogen beyond the western Mediterranean basin and current infection areas and pin-point populations at risk in the near future.


A total of 251 observations from September 2016 to April 2018 reported by the Mediterranean scientific network were combined with the 170 observations by citizens (June 2017–April 2018; ~26 monthly observations) to yield a total of 421 observations (40.38 and 59.62% reported by citizens vs. scientists respectively; Fig. 1 and Table A in Supplementary Material). Initially 289 observations were reported from the sea-watchers’ platform, which were scrutinized by expert scientists to filter out possible confusions between congeneric species P. nobilis and P. rudis as well as other kind of errors in the reports by sea-watchers. The spatio-temporal representation of this combined data set (Fig. 2) points to the southern part of the Iberian Peninsula as the first region where the MME was detected (Fig. 2A), while the Balearic Islands were the second area affected by this severe mortality in a relatively short time (Fig. 2B). Later, and after a relatively long period of time (8 months), the signs of the disease were sequentially detected on a northward trajectory along the Valencian coast (Fig. 2C,D). At the end of 2017, the MME was observed on the Catalan coast and beyond Spanish waters in some sites around Corsica (Fig. 2E). During the first months of 2018, mortality was observed at specific sites along the Italian coast (Fig. 2F). However, specific localities in the Mediterranean Sea still harboured P. nobilis populations in good condition for the duration of this mortality wave (from September 2016 to April 2018). For example, no signs of the disease have been detected at the Mar Menor coastal lagoon and Ebro Delta areas (highlighted with blue circles in Fig. 2C,F), despite the fact that there was 100% mortality in the surrounding areas. Similarly, in the entire Central and Eastern Mediterranean P. nobilis populations remained unaffected until April 2018 (Figs 1A,B and 2A in Supplementary Material).

Figure 1

Observations of P. nobilis health conducted by citizens (yellow circles) vs. scientists (blue circles), with zoomed in areas where most observations were done.

Figure 2

Disease observations based on the health status of P. nobilis (Dead/ill vs. alive, represented by red diamonds and green circles respectively) for the whole period from September 2016 to April 2018 (A). Spatio-temporal zooms of such observations are represented in panels B–F. Note that the crossed yellow point indicates the zone where the mortality was observed for the first time (Mass Mortality Event First Observation; MME_FOb), blue empty circles surround Healthy Populations (HP) and orange arrows denote Disease Observations Sequence (DOS).

The model current simulations suggest that the parasite Haplosporidium pinnae has probably dispersed regionally by currents (mp4 animation in Supplementary Material and Fig. 3). The backward trajectories ending on the southern coast of Mallorca (p2 at Fig. 3) in October 2016 indicate a possible origin along the coast of Alicante and Murcia, which is in agreement with the observations of the disease (orange trajectories at Fig. 3). Moreover, the transit time is consistent with the observations, showing only a 1-day difference between the average arrival time at p2 and the observed date (average time; Table 1). A similar agreement is found in the second simulation using forward trajectories from the Ebro River area in June 2017 (blue trajectories in Fig. 3). A slow northward propagation is described in the model, with an average time of arrival of the particles in the final point (p2) 3 days before the observed infection (Table 1). This agreement in both simulations is quite remarkable given the uncertainties inherently present in the model predictions. As mentioned in Section 4.2, the cluster approach provides a way to take into account these uncertainties. The backward simulation shows a wide range of possible departure times, with an average approximately at the observed date as the first particle left p1 19 days before and last particle left p1 18 days after the observed date (Table 1), providing insights into the range of possible scenarios for particle drifts given specific surface current conditions over a period of several weeks. The simulated departure dates for L’Ametlla de Mar are more skewed, as the first particle arrives to p2 19 days before and last particle left p2 10 days after the observed infection date (Table 1). The third simulation providing forward trajectories from a location along the Catalan coast in December 2017 (purple trajectories at Fig. 3) indicates an overall south-eastward dispersion towards Mallorca, Menorca, Corsica and Sardinia islands, and the Algero-Provençal basin. Some of the particles still reached the area of observed infection, with an average arrival 26 days before the observed infection date. The last particle reaching p2 arrived only 3 days before the observed infection (Table 1). Even if the agreement is not as good as in the two previous cases, these results still support the hypothesis of disease dispersion by surface currents given the uncertainties present in the model and observations.

Figure 3

Drift simulations: backward simulations in the Balearic Islands area (orange path), forward simulations at L’Ametlla de Mar area (blue path) and, forward simulations at the north Catalonia area (purple path). Note that points at the end of the paths indicate the particle final position. Simulations were inferred between point 1 (p1; infected point) and point 2 (p2; no signs of infection at the beginning of the simulation and infection at a known time interval of the simulation). The rectangle indicates 650 km2 buffer zone around a given point.

Table 1 Observed vs. estimated dates for the arrival of particles subset at buffer areas in the three drift simulations conducted.

After arrival to local sites, temperature and salinity appear to be decisive in the development of the disease (p < 0.01 and p < 0.001, respectively; 69.5% deviance explained) according to the GAM model. In fact, the disease expression (pen shell dead or ill) seems to be closely related to temperatures above 13.5 °C and with a salinity range between 36.5 and 39.7 psu (Fig. 4).

Figure 4

Partial smoothed effect of Temperature (A) and Salinity (B) on the disease expression (note that zero marks the shift on the response; >0 corresponds to higher probability of disease absence, while <0 to higher probability of disease expression). Fitted lines (solid line), 95% confidence intervals (shaded area) and partial residuals (hollow points) are shown for univariate effects. Top and bottom tick marks on x-axis represent values of the observed covariable for the absence and presence of signs of infection respectively.


Assuming that the mass mortality events described in this study have been caused by the newly described parasite H. pinnae27, model simulations of particle drift dictated by regional surface currents suggest that parasite dispersion by surface currents could play an important role at a regional scale, as has been suggested before for other Haplosporidian species44. Despite the lack of resistant forms in Bonamia species (sporal stage or sporulation process have never been detected27), some studies support that B. ostreae and B. exitiosa spread via water currents and strong tide currents42,47 contributing to a rapid expansion but with a reduced spatial range (within a bay or in sites sharing commune water bodies but with reduced survival of the cells outside the host47). Such constricted dispersion does not seem likely for the pattern of parasite dispersion in this study, where the spores of H. pinnae would be dispersed over long distances for an extended time period (at least for a few weeks; Fig. 3 and mp4 animation in Supplementary Material). However, this hypothesis is compatible with Haplosporidians with a sporal stage, since though dispersal in most such parasite species (e.g., H. nelsoni) is poorly understood and remains purely speculative, several studies suggest that dispersion by currents is the most plausible dispersion mode33,48. Spores or at least sporulation of the pen shell parasite H. pinnae have been detected in the epithelium of digestive tubules27,31, and spore ornamentations, which may aid in flotation49, have been detected in other molluscan protozoan parasites49. Therefore, the presence of such resistant spores with attachments (e.g., long tape-like filaments attached to the spore wall) possibly providing buoyancy27 in the life-cycle of H. pinnae, suggests that this parasite could be readily dispersed by currents - the remarkable agreement obtained in this study between the arrival of virtual particles and observed infection at sites strongly supports this hypothesis. Alternatively, there could be a hypothetical involvement of planktonic species50 as an intermediate host, as suggested for H. nelsoni and H. costale33,51. The intrinsic uncertainty of the model linked to the turbulent nature of ocean flows and the existence of fine-scale littoral processes that remain unresolved in the model inevitably generate uncertainties in the computation of ocean trajectories. A major outcome of the modelling study was that some areas were successively infected with a time delay in reasonable agreement with the observations, which indicates that surface currents could act as a main driver for the transport of the parasite across the Mediterranean basin. Moreover, not only model simulations, but also the very limited knowledge of certain key stages of the parasite life cycle could be a potential uncertainty source. At the moment, the time-frame from parasite colonization of a given area and infection and virulence in the host is unknown; therefore pen shells might be infected for some time before showing signs of disease. This means that both scientists and sea-watchers only detect the infection when P. nobilis shows signs of disease (e.g., pale and withdrawn mantle, valves that do not close or do it very slowly), but the parasite could have the ability of infecting the pen shell some days, weeks or even months before. Moreover, an unknown time could elapse between the infection and the death of P. nobilis. These un-estimated and unknown time-steps could induce a potential bias causing the uncertainty and discrepancy between observations and predictions. Similarly, the origin of this parasite is speculative because of the limited information available for some areas such as the North-African coast. For instance, a die-off has been detected in certain counties along that coastline, but the timing of this event is completely unknown, which constricts our capacity to identify the exact source of the infection. Further uncertainty is also associated to the role and origin of the Mycobacteria species recently found in two regions of Italy and associated to mass mortality events of P. nobilis29. In otherwise healthy individuals, significant mortality (up to 82%) appears to be associated to the presence of Vibrio mediterranei and its degree of pathogenicity is currently under investigation (P. Prado, pers. communication).

The dynamics of Haplosporidian parasites is modulated by environmental conditions44 and therefore also the prevalence of H. pinnae after its arrival by currents at a given area is subject to the environmental conditions in such area. Based on our modelling results, the expression of disease seems to be related to temperatures above 13.5 °C and a salinity range between 36.5–39.7 psu, although the upper limit of the salinity should not be considered accurate due to the lack of such data (salinities above 38.5 psu) - monitoring further dispersal of the parasite in the eastern Mediterranean, where prevailing salinities are higher than in the western Mediterranean, will allow the accurate estimation of the upper salinity limit. A similar pattern has been also observed for other Haplosporidians parasites. For example, the congeneric species H. nelsoni is highly sensitive to temperature and salinity, which influence both its geographic distribution and seasonal infection patterns32,36,37. Specifically, field and in vitro experiments demonstrated that the ability of H. nelsoni to proliferate or survive decreases at lower salinities38 and its prevalence and virulence is affected seasonally by temperature oscillations; its prevalence decreases in the late winter, due to the exposure to low temperatures39. B. exitiosa shows a similar pattern of tolerance of environmental conditions40,41. However, B. ostreae showed higher survival outside its host and viability at lower temperatures (4–15 °C than at 25 °C), although the same positive relationship was observed regarding disease prevalence and salinity (higher prevalence at salinities >35 psu than <20 psu)42. These patterns suggest a species-specific tolerance to environmental conditions44, and could explain why, despite infection of the surrounding areas (with extinct populations), there are areas that shelter P. nobilis populations that are still in good condition. This is quite probably due to the salinity range outside the common Mediterranean salinity range of 36.7–39.5 psu52; this is the case, for example, of Alfacs Bay, strongly affected by discharges of the Ebro River53,54, and the Mar Menor coastal lagoon, a confined area with high salinity up to 40 psu55. However, it is important to remark that pen shells living in the Mar Menor lagoon or Alfacs Bay are vulnerable populations since changes in water conditions (currents, salinity and temperature) can still lead to the disappearance of those populations by a sudden exposure to the parasite or by increased virulence. Similarly, the observation of healthy P. nobilis populations at the northernmost Catalan Coasts and French Coasts in April 2018 (Fig. 2F) were probably related to the fact that the arrival of the parasite coincided with un-favourable low-winter temperatures (<13.5 °C56). In fact, by May 2018, when temperatures increased above 13.5 °C, mass mortalities were detected in these populations (pers. com. García-March).

In the last decades, the participation of citizens in science has experienced an exponential growth, probably due to the ecological awareness and the wide range of possibilities offered by the latest technologies (e.g, web portals, mobiles, apps to report live observations57). In this study, citizen science has played an essential role in the follow-up of a mass mortality event with a rapid expansion across an extensive area (western Mediterranean basin). Citizen science can overcome the logistics barriers of scientific monitoring, contributing with several observations at high spatial-temporal scales, as for example to track disease-carrying tiger mosquitoes46. However, citizen observations require a strict quality control for the reliability of data reported58,59. In our case, a scientific team was involved in the carefully validation of each citizen observation based on: (i) the experience of sea-watcher (e.g., scuba diving instructor vs. kayak fan, the first with a supposed better experience observing pen shells), (ii) complementary information (e.g., habitat type, with rocky bottoms the essential habitat for the congeneric species P. rudis) and, essentially, with (iii) photographic evidence (the most important and essential additional information for validation). In fact, more than half of the reported observations of healthy P. nobilis were removed (58.82%) after being carefully scrutinized by the scientific team. Most of such errant observations made reference to a very similar species; P. rudis. This congeneric species remains in good health conditions and seems to be resistant to the disease, with recent mortality rates according to its natural rates, and not higher than before the outbreak6,60. However it is difficult to discern between species due to anatomical similitudes3. When the technological problems of sharing observations are overcome, future efforts should be focused on minimizing the hard work of manually filtering citizens’ observations58. Notwithstanding the applicability of citizen observations, the best solution would appear to be the combination of citizen science with traditional scientific methods that combine tracking of mortality events in sentinel populations with detection of H. pinnae, allowing the two approaches to complement each other46. Therefore not only validation of layman observations, but also a coordinated, scientific monitoring program for the Mediterranean would be beneficial to follow the spread of mortality events.

Overall, our results point to a challenging scenario for the conservation of the emblematic P. nobilis. Most likely, currents will carry the parasite along the whole Mediterranean basin, and are already reaching the healthy populations of the central (e.g., Sardinia - June 2018; pers. com. Coppa) and eastern Mediterranean (e.g., Lesvos Island, Greece - August 201828). In addition, the dispersal of the disease to distant localities could be assisted by vessels through their ballast waters, which constitutes one of the major vectors of primary and secondary introduction of alien species in the Mediterranean61. The extreme virulence of H. pinnae26,27,28 will probably devastate P. nobilis populations, except for populations confined in areas with environmental conditions beyond the tolerance limits of the parasite (constant low-temperatures and abnormally high or low salinity values) or the potential resistant individuals. The high genetic homogeneity of Mediterranean pen shell populations, with little differentiation between recently disappeared populations in more “open” waters and these scattered survival spots62, seriously compromises the recovery of the species as they likely share the same susceptibility for the parasite. Also, the inbreeding coefficient (FIS) was positive and significant at the western Mediterranean locations62. Inbreeding can greatly reduce the average individual fitness, and loss of genetic variability from random genetic drift can diminish future adaptability to a changing environment63. Despite the theoretical possibility that spots with surviving populations could act as a larval source for the spread of the species in larger areas62, this is only possible if they act as source populations, there is a favourable connection between these sites by local currents64, and recruits meet with parasite-free conditions in the localities of settlement. Another possible source for the recovery of populations might be the presence of surviving resistant individuals. However, this possibility seems to be compromised by several bottle-necks. Even if now and then there are sightings of healthy and maybe resistant individuals, they are extremely scattered, reducing the probability of reproduction among them (as male and female gametes are released to the water column and fertilization is external21), so relatively dense populations might be needed to assure successful fertilization. In the case of overcoming this reproductive handicap, if the scattered resistant individuals were able to produce some recruits, their natural mortality would be very high, because the species is extremely vulnerable to predators when young6,14. Furthermore, the pen shell’s slow growth-rate and dynamics (e.g., only individuals larger than 37 cm of shell length -at least 4 years old- released gametes in experimental conditions65) turn this species highly vulnerable to catastrophic events and predict a very slow recovery of the species even if recruits manage to establish in infected areas. Therefore, it is crucial to act while there are still specimens in healthy conditions, and to protect and monitor surviving individuals. As illegal harvesting of P. nobilis still occurs in many Mediterranean countries (e.g.66), better enforcement of the legislation for the protection of the species and actions for public awareness are needed to protect unaffected populations. The participation of citizens in protection campaigns and the monitoring of the status of populations all over the Mediterranean basin can play a key role.

Material and Methods

Data collection

We compiled data on mortality of pen shell populations starting from the first MME warning (28th September of 2016 at Ibiza, Balearic Islands, Spain; crossed yellow point at Fig. 2A) to April 2018. Scientific data was compiled from: (i) data published in different scientific documents26,67,68 and (ii) scuba diving monitoring of pen shell populations conducted by most of the scientific groups involved in the study of the P. nobilis (expert network). In order to complement the scientific data with multiple and simultaneous observations at many sites, a module open to citizens was added to (project NACRAS; launched on 2th of June of 2017) the website: (translated in English as “sea-watchers”). This platform allows citizens to report their observations about pen shell sightings and health state (alive, dead, or ill; the latter defined as a slow closing response of the valves or a pale and withdrawn mantle) with some complementary information (a spatio-temporal reference; date and GPS coordinates, temperature, salinity, depth, and habitat). After uploading an observation, the scientific team of the module curated each record based on sea-watcher experience, availability of complementary information and/or un uploaded photo, and frequently, through a dialogue with the sea-watcher.

From these sources, essential information like recent abnormal mortality, date, GPS coordinates, temperature, salinity, and depth were extracted for each observation to fit predictive models (see section Data analyses below). A trustworthy curated observation of one individual of a population reported as dead or ill under suspicious (not by predators, anchoring etc.) conditions was included in the model. Temperature and salinity data were extracted from the nearest available point of the database ‘EN4.2.1: quality controlled subsurface ocean temperature and salinity profiles and objective analyses’ (downloaded from on April 30th 201869) except for sites where hydrographic values were carefully measured in situ by scientists (e.g., the Mar Menor coastal lagoon, the Alfacs Bay affected by River Ebro discharges). The EN4.2.1 dataset contains monthly objective analysis of temperature and salinity with the corrections69 in a 1-degree grid and 42 different depths (from 5 m to 5000 m), spanning a period from 1900 to present.

Data analyses

The potential role of the surface currents on the expansion of the disease was investigated simulating the drift of 1000 virtual particles (Par) in a high-resolution regional model of the western Mediterranean Sea, the WMOP model70,71. This model is developed and operated by SOCIB, the Balearic Islands Coastal Observing and Forecasting System. The WMOP model provides daily predictions of hydrodynamic conditions with a 2-km resolution from the Strait of Gibraltar to Corsica and Sardinia. It is a regional implementation of the Regional Ocean Modelling System (ROMS72), downscaling simulations from the Copernicus Marine Service Mediterranean model, and forced by the high resolution HIRLAM model from the Spanish Meteorological Agency. Details of the operational system can be found in70,71. An important aspect of this system is the multi-platform evaluation of the model predictions using available in situ and satellite observations, both in real-time and delayed modes70,71, including daily validation updates provided on SOCIB website. The surface currents predicted by the operational model in 2016 and 2017 were used to simulate the drift of virtual particles from locations and times associated with observations of infected P. nobilis during the following 45 days. The TRACMASS algorithm73 was used to generate the Lagrangian trajectories. A cluster of 1000 particles was seeded at each starting location, and advected by model surface currents plus a diffusive term adding a random displacement at each time step to account for model uncertainties and unresolved processes. Simulations were performed both in forward and backward modes to track the potential destination and provenance of the particles as described by the model surface current conditions. More concretely, simulations of currents were conducted in areas and within time-intervals (t0, … tn; time in days) where the arrival of the disease (final time; tf) at a given point (pi) was detected by observations of first absence of mortality (pen shell alive at pit0) and then indications of mortality by probable infection (pen shell dead or ill at pitf). Given the available dataset, one backward simulation (from 2016/10/24 to 2016/09/09 in the Balearic Islands) and two forward simulations (from 2017/06/09 to 2017/07/24 in the L’Ametlla de Mar area and from 2017/10/27 to 2017/12/11 in North Catalonia) were produced in order to analyse the time for a particle to drift: (i) from p1 (visible mortality at p1t0) to p2 (no infection observed at p2t0 and mortality at p2tf) in the case of forward simulations (tracking particles destination), and inversely, (ii) from p2tf to p1 in the case of backward simulation (tracking particles provenance). To predict the beginning of a local mortality event at a given point (p1 or p2 in the case of backward or forward simulation, respectively), the subset of simulated particles drifting within a buffer zone of 650 km2 around selected point (as center of such buffer zone) were selected before extracting the final time (arrival time; tf) of each of these particles. These predicted times were compared checking the time delay between empirical dates of P. nobilis infected in the starting (p1) and ending locations (p2).

The relationship with establishment success of the disease after arrival and environmental variables was addressed using a generalized additive model (GAM) with the gam function of the mgcv library within R software74. GAMs extend general linear models allowing for complex correlations between response and explanatory variables75. In this sense, the potential effect of temperature (Temp) and salinity (Sal) on the presence/absence of the disease (Disease) was tested fitting a binomial GAM [Disease~ s(Temp) + s(Sal)]. It is important to highlight that a subset of data was selected to fit the GAM (n = 271 observations; 232 presence and 39 absence of disease). Only data with a probable spatio-temporal prevalence of the disease were selected, avoiding the bias caused by the spatio-temporal absence of the disease (e.g., data from Eastern Mediterranean where the disease has not yet been detected and the P. nobilis populations are still healthy).


  1. 1.

    Vicente, N. Estudio ecológico y protección del molusco lamelibranquio Pinna nobilis L., 1758 en la costa mediterránea. Iberus 9, 269–279 (1990).

    Google Scholar 

  2. 2.

    Zavodnik, D., Hrs-Brenko, M. & Legac, M. Synopsis on the fan shell Pinna nobilis L. In the eastern Adriatic Sea. in Les Espècies Marines à protéger en Méditerranée (eds Boudouresque, C. F., Avon, M. & Gravez, V.) 169–178 (GIS Posidonie publications, 1991).

  3. 3.

    Schulz, P. & Huber, M. Revision of the Worldwide Recent Pinnidae and some Remarks on Fossil European Pinnidae. Acta Conchyl. 13, 1–164 (2013).

    Google Scholar 

  4. 4.

    García-March, J. R., Garcia-Carrascosa, A. M. & Peña, A. L. In Situ Measurement of Pinna nobilis Shells for Age and Growth Studies: A New Device. Mar. Ecol. 23, 207–217 (2002).

    ADS  Article  Google Scholar 

  5. 5.

    Katsanevakis, S. Growth and mortality rates of the fan mussel Pinna nobilis in Lake Vouliagmeni (Korinthiakos Gulf, Greece): A generalized additive modelling approach. Mar. Biol. 152, 1319–1331 (2007).

    Article  Google Scholar 

  6. 6.

    Kersting, D. K. & García-March, J. R. Long-term assessment of recruitment, early stages and population dynamics of the endangered Mediterranean fan mussel Pinna nobilis in the Columbretes Islands (NW Mediterranean). Mar. Environ. Res. 130, 282–292 (2017).

    CAS  Article  Google Scholar 

  7. 7.

    Rouanet, E., Trigos, S. & Vicente, N. From youth to death of old age: the 50-year story of a Pinna nobilis fan mussel population at Port-Cros Island (Port-Cros National Park, Provence, Mediterranean Sea). Sci. Reports Port-Cros Natl. Park 29, 209–222 (2015).

    Google Scholar 

  8. 8.

    Trigos, S., García-March, J. R., Vicente, N., Tena, J. & Torres, J. Utilization of muddy detritus as organic matter source by the fan mussel Pinna nobilis. Mediterr. Mar. Sci. 15, 667–674 (2014).

    Article  Google Scholar 

  9. 9.

    Corriero, G. & Pronzato, R. Epibiontic sponges on the bivalve Pinna nobilis. Mar. Ecol. Prog. Ser. 35, 75–82 (1987).

    ADS  Article  Google Scholar 

  10. 10.

    Giacobbe, S. Epibiontic mollusc communities on Pinna nobilis L. (Bivalvia, Mollusca). J. Nat. Hist. 36, 1385–1396 (2002).

    Article  Google Scholar 

  11. 11.

    Addis, P. et al. Density, size structure, shell orientation and epibiontic colonization of the fan mussel Pinna nobilis L. 1758 (Mollusca: Bivalvia) in three contrasting habitats in an estuarine area of Sardinia (W Mediterranean). Sci. Mar. 73, 143–152 (2009).

    Article  Google Scholar 

  12. 12.

    Katsanevakis, S. Transplantation as a conservation action to protect the Mediterranean fan mussel Pinna nobilis. Mar. Ecol. Prog. Ser. 546, 113–122 (2016).

    ADS  Article  Google Scholar 

  13. 13.

    Fiorito, G. & Gherardi, F. Prey-handling behaviour of Octopus vulgaris (Mollusca, Cephalopoda) on Bivalve preys. Behav. Processes 46, 75–88 (1999).

    CAS  Article  Google Scholar 

  14. 14.

    García-March, J. R., García-Carrascosa, A. M., Peña Cantero, A. L. & Wang, Y. G. Population structure, mortality and growth of Pinna nobilis Linnaeus, 1758 (Mollusca, Bivalvia) at different depths in Moraira bay (Alicante, Western Mediterranean). Mar. Biol. 150, 861–871 (2007).

    Article  Google Scholar 

  15. 15.

    Rabaoui, L., Zouari, S. T. & Hassine, O. K. Ben. Two species of Crustacea (Decapoda) associated with the fan mussel, Pinna nobilis Linnaeus, 1758 (Mollusca, Bivalvia). Crustaceana 81, 433–446 (2008).

    Article  Google Scholar 

  16. 16.

    Sureda, A., Natalotto, A., Álvarez, E. & Deudero, S. Increased antioxidant response and capability to produce ROS in hemocytes of Pinna nobilis L. exposed to anthropogenic activity. Environ. Pollut. 181, 321–324 (2013).

    CAS  Article  Google Scholar 

  17. 17.

    Alomar, C., Vázquez-Luis, M., Magraner, K., Lozano, L. & Deudero, S. Evaluating stable isotopic signals in bivalve Pinna nobilis under different human pressures. J. Exp. Mar. Biol. Ecol. 467, 77–86 (2015).

    CAS  Article  Google Scholar 

  18. 18.

    Vázquez-Luis, M., Borg, J. A., Morell, C., Banach-Esteve, G. & Deudero, S. Influence of boat anchoring on Pinna nobilis: A field experiment using mimic units. Mar. Freshw. Res. 66, 786–794 (2015).

    Article  Google Scholar 

  19. 19.

    Hendriks, I. E. et al. Boat anchoring impacts coastal populations of the pen shell, The largest bivalve in the Mediterranean. Biol. Conserv. 160, 105–113 (2013).

    Article  Google Scholar 

  20. 20.

    Katsanevakis, S. Population dynamics of the endangered fan mussel Pinna nobilis in a marine lake: A metapopulation matrix modeling approach. Mar. Biol. 156, 1715–1732 (2009).

    Article  Google Scholar 

  21. 21.

    Basso, L. et al. The Pen Shell, Pinna nobilis: A Review of Population Status and Recommended Research Priorities in the Mediterranean Sea. Adv. Mar. Biol. 71, 109–160 (2015).

    Article  Google Scholar 

  22. 22.

    Deudero, S., Vázquez-Luis, M. & Álvarez, E. Human stressors are driving coastal benthic long-lived sessile fan mussel Pinna nobilis population structure more than environmental stressors. PLoS ONE 10, e0134530 (2015).

    Article  Google Scholar 

  23. 23.

    Basso, L., Hendriks, I. E. & Duarte, C. M. Juvenile Pen Shells (Pinna nobilis) tolerate acidification but are vulnerable to warming. Estuaries and Coasts 38, 1976–1985 (2015).

    Article  Google Scholar 

  24. 24.

    Fey, S. B. et al. Recent shifts in the occurrence, cause, and magnitude of animal mass mortality events. Proc. Natl. Acad. Sci. 112, 1083–1088 (2015).

    ADS  CAS  Article  Google Scholar 

  25. 25.

    Langangen, Ø. et al. Cascading effects of mass mortality events in Arctic marine communities. Glob. Chang. Biol. 23, 283–292 (2017).

    ADS  Article  Google Scholar 

  26. 26.

    Vázquez-Luis, M. et al. S.O.S. Pinna nobilis: A Mass Mortality Event in Western Mediterranean Sea. Front. Mar. Sci. 4, 1–6 (2017).

    Article  Google Scholar 

  27. 27.

    Catanese, G. et al. Haplosporidium pinnae sp. nov., a haplosporidan parasite associated with mass mortalities of the fan mussel, Pinna nobilis, in the Western Mediterranean Sea. J. Invertebr. Pathol. 157, 9–24 (2018).

    CAS  Article  Google Scholar 

  28. 28.

    Katsanevakis, S. et al. The cryptogenic parasite Haplosporidium pinnae invades the Aegean Sea and causes the collapse of Pinna nobilis populations. Aquat. Invasions 14, (2019).

    Article  Google Scholar 

  29. 29.

    Carella, F. et al. A mycobacterial disease is associated with the silent mass mortality of the pen shell Pinna nobilis along the Tyrrhenian coastline of Italy. Sci. Rep. 9, 2725 (2019).

    ADS  CAS  Article  Google Scholar 

  30. 30.

    Panarese, R. et al. Haplosporidium pinnae associated with mass mortality in endangered Pinna nobilis (Linnaeus 1758) fan mussels. J. Invertebr. Pathol. 164, 32–37 (2019).

    Article  Google Scholar 

  31. 31.

    Darriba, S. First haplosporidan parasite reported infecting a member of the Superfamily Pinnoidea (Pinna nobilis) during a mortality event in Alicante (Spain, Western Mediterranean). J. Invertebr. Pathol. 148, 14–19 (2017).

    Article  Google Scholar 

  32. 32.

    Ford, S. E. & Haskin, H. H. History and epizootiology of Haplosporidium nelsoni (MSX), an oyster pathogen in Delaware Bay, 1957-1980. J. Invertebr. Pathol. 40, 118–141 (1982).

    Article  Google Scholar 

  33. 33.

    Haskin, H. H. & Andrews, J. D. Uncertainties and speculations about the life cycle of the eastern oyster pathogen Haplosporidium nelsoni (MSX). Dis. Process. Mar. Bivalve Molluscs 18, 5–22 (1988).

    Google Scholar 

  34. 34.

    Hudson, E. B. & Hill, B. J. Impact and spread of bonamiasis in the UK. Aquaculture 93, 279–285 (1991).

    Article  Google Scholar 

  35. 35.

    Laing, I., Dunn, P., Peeler, E. J., Feist, S. W. & Longshaw, M. Epidemiology of Bonamia in the UK, 1982 to 2012. Dis. Aquat. Organ. 110, 101–111 (2014).

    CAS  Article  Google Scholar 

  36. 36.

    Hofmann, E., Ford, S., Powell, E. & Klinck, J. Modeling studies of the effect of climate variability on MSX disease in eastern oyster (Crassostrea virginica) populations. Hydrobiologia 460, 195–212 (2001).

    Article  Google Scholar 

  37. 37.

    Burreson, E. M. & Ford, S. E. A review of recent information on the Haplosporidia, with special reference to Haplosporidium nelsoni (MSX disease). Aquat. Living Resour. 17, 499–517 (2004).

    Article  Google Scholar 

  38. 38.

    Ford, S. E. & Haskin, H. H. Comparison of in vitro salinity tolerance of the oyster parasite, Haplosporidium nelsoni (msx) and hemocytes from the host, Crassostrea virginica. Comp. Biochem. Physiol.–Part A Physiol. 90, 183–187 (1988).

    Article  Google Scholar 

  39. 39.

    Andrews, J. D. Epizootiology of late summer and fall infections of oysters by Haplosporidium nelsoni, and comparison to annual life cycle of Haplosporidium costalis, a typical haplosporidan. J. Shellfish Res. 2, 15–23 (1982).

    Google Scholar 

  40. 40.

    Hine, P. M. Severe apicomplexan infection in the oyster Ostrea chilensis: A possible predisposing factor in bonamiosis. Dis. Aquat. Organ. 51, 49–60 (2002).

    CAS  Article  Google Scholar 

  41. 41.

    Audemard, C., Carnegie, R. B., Hill, K. M., Peterson, C. H. & Burreson, E. M. Bonamia exitiosa transmission among, and incidence in, Asian oyster Crassostrea ariakensis under warm euhaline conditions. Dis. Aquat. Organ. 110, 143–150 (2014).

    CAS  Article  Google Scholar 

  42. 42.

    Arzul, I. et al. Effects of temperature and salinity on the survival of Bonamia ostreae, a parasite infecting flat oysters Ostrea edulis. Dis. Aquat. Organ. 85, 67–75 (2009).

    CAS  Article  Google Scholar 

  43. 43.

    Arzul, I. et al. Bonamia ostreae and Ostrea edulis: a stable host-parasite system in France? XI International Symposium for Veterinary Epidemiology and Economics, Cairns, Queensland, Australia, 6–11 August 2006. (2006).

  44. 44.

    Arzul, I. & Carnegie, R. B. New perspective on the haplosporidian parasites of molluscs. J. Invertebr. Pathol. 131, 32–42 (2015).

    Article  Google Scholar 

  45. 45.

    Levin, S. A. The problem of pattern and scale in ecology. Ecology 73, 1943–1967 (1992).

    Article  Google Scholar 

  46. 46.

    Palmer, J. R. B. et al. Citizen science provides a reliable and scalable tool to track disease-carrying mosquitoes. Nat. Commun. 8, 1–12 (2017).

    ADS  Article  Google Scholar 

  47. 47.

    Kroeck, M. A., Semenas, L. & Morsan, E. M. Epidemiological study of Bonamia sp. in the native flat oyster, Ostrea puelchana from San Matías Gulf (NW Patagonia, Argentina). Aquaculture 276, 5–13 (2008).

    Article  Google Scholar 

  48. 48.

    Ford, S. E., Allam, B. & Xu, Z. Using bivalves as particle collectors with PCR detection to investigate the environmental distribution of Haplosporidium nelsoni. Dis. Aquat. Organ. 83, 159–168 (2009).

    Article  Google Scholar 

  49. 49.

    Barber, R. D. & Ford, S. E. Occurrence and significance of ingested haplosporidan spores in the eastern oyster, Crassostrea virginica (Gmelin, 1791). J. Shellfish Res. 11, 371–375 (1992).

    Google Scholar 

  50. 50.

    Messerman, N. A. & Bowden, T. J. Survey of potential reservoir species for the oyster parasite Multinucleate Sphere X (Haplosporidium nelsoni) in and around oyster farms in the Damariscotta River Estuary, Maine. J. Shellfish Res. 35, 851–856 (2016).

    Article  Google Scholar 

  51. 51.

    Powell, E. N., Klinck, J. M., Ford, S. E., Hofmann, E. E. & Jordan, S. J. Modeling the MSX parasite in eastern oyster (Crassostrea virginica) populations. III. Regional application and the problem of transmission. J. Shellfish Res. 18, 517–537 (1999).

    Google Scholar 

  52. 52.

    Vidal-Vijande, E., Pascual, A., Barnier, B., Molines, J.-M. & Tintoré, J. Analysis of a 44-year hindcast for the Mediterranean Sea: comparison with altimetry and in situ observations. Sci. Mar. 75, 71–86 (2011).

    Article  Google Scholar 

  53. 53.

    Prado, P., Caiola, N. & Ibáñez, C. Habitat use by a large population of Pinna nobilis in shallow waters. Sci. Mar. 78, 555–565 (2014).

    Article  Google Scholar 

  54. 54.

    Salat, J. & Cruzado, A. Masses d’eau dans la Méditerranée occidentale: Mer Catalane et eaux adjacentes. Rapp. Comm. Int. pour l’exploration Sci. la mer Méditerranée 27, 201–209 (1981).

    Google Scholar 

  55. 55.

    Pérez-Ruzafa, Á., Marcos, C. & Gilabert, J. The ecology of the Mar Menor Coastal Lagoon: a fast changing ecosystem under human pressure. In Coastal lagoons. Ecosystem processes and modeling for sustainable use and development (eds Gönenç, I. E. & Wolflin, J. P.) 392–422 (CRC Press Boca Raton, 2005).

  56. 56.

    Vargas-Yáñez, M. et al. Updating temperature and salinity mean values and trends in the Western Mediterranean: The RADMED project. Prog. Oceanogr. 157, 27–46 (2017).

    ADS  Article  Google Scholar 

  57. 57.

    Dickinson, J. L. et al. The current state of citizen science as a tool for ecological research and public engagement. Front. Ecol. Environ. 10, 291–297 (2012).

    Article  Google Scholar 

  58. 58.

    Kosmala, M., Wiggins, A., Swanson, A. & Simmons, B. Assessing data quality in citizen science. Front. Ecol. Environ. 14, 551–560 (2016).

    Article  Google Scholar 

  59. 59.

    Wiggins, A., Newman, G., Stevenson, R. D. & Crowston, K. Mechanisms for data quality and validation in citizen science. Proceedings - 7th IEEE International Conference on e-Science Workshops, eScienceW 2011, 14–19, (2011).

    Article  Google Scholar 

  60. 60.

    Nebot-Colomer, E., Vázquez-Luis, M., Gracía-March, J. R. & Deudero, S. Population Structure and Growth of the Threatened Pen Shell, Pinna rudis (Linnaeus, 1758) in a Western Mediterranean Marine Protected Area. Mediterr. Mar. Sci. 17, 785 (2016).

    Article  Google Scholar 

  61. 61.

    Zenetos, A. et al. Alien species in the Mediterranean Sea by 2012. A contribution to the application of European Union’s Marine Strategy Framework Directive (MSFD). Part 2. Introduction trends and pathways. Mediterr. Mar. Sci. 13, 328–352 (2012).

    Article  Google Scholar 

  62. 62.

    Wesselmann, M. et al. Genetic and oceanographic tools reveal high population connectivity and diversity in the endangered pen shell Pinna nobilis. Sci. Rep. 8, 4770 (2018).

    ADS  Article  Google Scholar 

  63. 63.

    Lande, R. Genetics and demography in biological conservation. Science 241, 1455–1460 (1988).

    ADS  CAS  Article  Google Scholar 

  64. 64.

    González-Wangüemert, M. et al. Gene pool and connectivity patterns of Pinna nobilis in the Balearic Islands (Spain, Western Mediterranean Sea): Implications for its conservation through restocking. Aquat. Conserv. Mar. Freshw. Ecosyst. 29, 175-–188 (2018).

    Article  Google Scholar 

  65. 65.

    Trigos, S. Estudio de la ecofisiología y ensayo de cultivio de la nacra Pinna nobilis Linnaeus, 1758. (Universidad Católica de Valencia, 2017).

  66. 66.

    Katsanevakis, S. et al. ‘Protected’ marine shelled molluscs: Thriving in Greek seafood restaurants. Mediterr. Mar. Sci. 12, 429–438 (2011).

    Article  Google Scholar 

  67. 67.

    Vázquez-Luis, M. et al. Situación actual de Pinna nobilis en España. Nuevos datos de mortandad, individuos vivos y captación de juveniles. Not. SEM 68, 63–66 (2017).

    Google Scholar 

  68. 68.

    La, S. E. M. nacra Pinna nobilis. Not. SEM 67, 36–53 (2017).

    Google Scholar 

  69. 69.

    Good, S. A., Martin, M. J. & Rayner, N. A. EN4: Quality controlled ocean temperature and salinity profiles and monthly objective analyses with uncertainty estimates. J. Geophys. Res. Ocean. 118, 6704–6716 (2013).

    ADS  Article  Google Scholar 

  70. 70.

    Juza, M. et al. SOCIB operational ocean forecasting system and multi-platform validation in the Western Mediterranean Sea. J. Oper. Oceanogr. 9, s155–s166 (2016).

    Google Scholar 

  71. 71.

    Mourre, B. et al. Assessment of high-resolution regional ocean prediction systems using multi-platform observations: illustrations in the Western Mediterranean Sea. In New Frontiers in Operationl Oceanography (eds Chassignet, E., Verron, J., Pascual, A. & Tintoré, J.) (2018).

  72. 72.

    Shchepetkin, A. F. & McWilliams, J. C. The regional oceanic modeling system (ROMS): a split-explicit, free-surface, topography-following-coordinate oceanic model. Ocean Model. 9, 347–404 (2005).

    ADS  Article  Google Scholar 

  73. 73.

    Döös, K., Kjellsson, J. & Jönsson, B. TRACMASS—A Lagrangian Trajectory Model BT - Preventive Methods for Coastal Protection: Towards the Use of Ocean Dynamics for Pollution Control. In (eds Soomere, T. & Quak, E.) 225–249 (Springer International Publishing, 2013).

    Chapter  Google Scholar 

  74. 74.

    Wood, S. N. Generalized Additive Models: An Introduction with R. Chapman& Hall/CRC, Boca Rat. 391 pp., 10.1111/j.1541-0420.2007.00905_3.x (2006).

  75. 75.

    Hastie, T. & Tibshirani, R. Generalized Additive Models. Stat. Sci. 1, 297–310 (1986).

    MathSciNet  Article  Google Scholar 

Download references


The authors are very grateful to all citizens (sea-watchers) who reported their observations and improved data collection. This study was financed by the special action project “NACRAS – Evaluación de la magnitud de un evento de mortalidad combinando censos científicos ampliados con observaciones de ciencia ciudadana” co-funded by the Regional Government and Direcció General d’Innovació i Recerca of the Balearic Islands and the European Social Fund 2014–2020. Salinity and temperature data at Alfacs Bay was provided from the “Programa de Seguimiento de la calidad de las aguas, moluscos y fitoplancton tóxico en las zonas de producción de marisco del litoral catalán (PSQAM) de la DGPAM.” The authors acknowledge the MEDCLIC project, funded by “La Caixa” Foundation, contributing to the development of the WMOP hydrodynamic model. Maite Vázquez-Luis and Miguel Cabanellas-Reboredo were supported by a postdoctoral contract co-funded by the Regional Government of the Balearic Islands and the European Social Fund 2014–2020. Also, Vázquez-Luis was also supported by a postdoctoral contract Juan de la Cierva-Incorporación (IJCI-2016-29329) of Ministerio de Ciencia, Innovación y Universidades. Elvira Álvarez was supported by a Personal Técnico de Apoyo contract (PTA2015-10829-I) funded by the Spanish Ministry of Economy and Competiveness. Iris E. Hendriks was supported by Ramon y Cajal Fellowship RYC-2014-14970, cofunded by the Conselleria d’Innovació, Recerca i Turisme of the Balearic Government (Pla de ciència, tecnologia, innovació i emprenedoria 2013-2017) and the Spanish Ministry of Economy, Industry and Competitiveness. Jose Rafael Garcia-March and Jose Tena were supported by the project BF/HEM 15-1662 -The study, protection and possible breeding of pen shell (Pinna nobilis) in the Boka Kotorska bay (Montenegro) of the Prince Albert II of Monaco Foundation.

Author information




Original idea and planning I.E.H. and M.C.-R. Implementation of the hydrodynamic model and computation of the particle trajectories by B.M. M.C.-R. analysed the data and prepared the figures. M.C.-R. and I.E.H. interpreted the data and wrote the first draft. I.E.H., M.V.-L., and M.C.-R. prepared the revised manuscript. Á.A. helped design the animation provided in Supplementary Material section. M.C.-R., M.V.-L., E.Á., S.D., P.A., E.B., A.B., S.C., J.R.G.-M., S.G., F.G.C., L.H., S.V.J.-G., S.K., D.K.K., V.M., B.M., F.P.P., S.J.P., P.P., J.T.-M., J.deV., N.V., F.Z.B., and I.Z. participated in the fieldwork. All authors contributed to the writing of and reviewed the manuscript.

Corresponding author

Correspondence to Iris E. Hendriks.

Ethics declarations

Competing Interests

The authors declare no competing interests.

Additional information

Publisher’s note Springer Nature remains neutral with regard to jurisdictional claims in published maps and institutional affiliations.

Supplementary information

Rights and permissions

Open Access This article is licensed under a Creative Commons Attribution 4.0 International License, which permits use, sharing, adaptation, distribution and reproduction in any medium or format, as long as you give appropriate credit to the original author(s) and the source, provide a link to the Creative Commons license, and indicate if changes were made. The images or other third party material in this article are included in the article’s Creative Commons license, unless indicated otherwise in a credit line to the material. If material is not included in the article’s Creative Commons license and your intended use is not permitted by statutory regulation or exceeds the permitted use, you will need to obtain permission directly from the copyright holder. To view a copy of this license, visit

Reprints and Permissions

About this article

Verify currency and authenticity via CrossMark

Cite this article

Cabanellas-Reboredo, M., Vázquez-Luis, M., Mourre, B. et al. Tracking a mass mortality outbreak of pen shell Pinna nobilis populations: A collaborative effort of scientists and citizens. Sci Rep 9, 13355 (2019).

Download citation

Further reading


By submitting a comment you agree to abide by our Terms and Community Guidelines. If you find something abusive or that does not comply with our terms or guidelines please flag it as inappropriate.


Quick links

Nature Briefing

Sign up for the Nature Briefing newsletter — what matters in science, free to your inbox daily.

Get the most important science stories of the day, free in your inbox. Sign up for Nature Briefing