In July 2006 and 2016, the presence of P. oceanica seedlings was recorded in three localities (Figure 1) along the coasts of Corsica (France): Gulf of Saint Florent (2006), Gulf of Ventilegne (2016), and Tonnara (2016). In each of the first two localities, the density of seedlings was estimated by counting the number of seedlings in 10 quadrats (50 cm × 50 cm) randomly allocated in two sites, 100s of meters apart. Only one site was available at Tonnara. Seedlings were distinguished in the field from isolated shoots established from vegetative fragments owing to the presence of the seed or seed coat still attached to the rhizome and shorter leaves (<15 cm in length). The age of seedlings was determined on the basis of the total number of leaves (plus sheaths) per shoot, and the presence and color of the seed. We defined as newly established seedling (<1 year) a single shoot with 4–10 leaves and an attached a green seed, while we defined as well-established seedling (>1 year) as a single shoot with more than 10 leaves and an attached dark seed.

To evaluate the capacity of seedlings to establish new patches and colonize new substrate, six randomly selected seedling patches (three patches on sand and three patches on rock) observed in one site of the Gulf of Ventilegne (Balestri and Lardicci, 2008) were marked at their edge and photographed in July 2005. At the start of the monitoring period, the shape of these patches was approximately circular, and their maximum width varied from 0.15 to 40 cm. To monitor their evolution, the patches were followed yearly till July 2016 by visual inspections and photographs.

We searched all papers (peer-reviewed articles, gray literature and personal communications from other authors) that provide direct or indirect evidence of natural establishment of P. oceanica seedlings in the electronic library databases (e.g., Web of Science, Thomson Reuters, New York, NY, United States and Google, Mountain View, CA, United States). Two sets of keywords were used. The first set included words the associated with the seagrass (seagrass) or scientific name (Posidonia oceanica). The second set of keywords contained words associated with sexual reproduction (sexual reproduction, recruitment, seedling, or flowering). Each word in the first set was searched in combination with each word from the second set (last search date: 05/10/2016). In addition, to take into account older references that may not be available through ISI Web of Science, the reference list in each article was also scanned for any other relevant publications or unpublished observation. Delocalized citations (seedlings stranded on beaches or floating) were also examined even if not considered as successful recruitment.

From all available reports and our own unpublished data on the recruitment of P. oceanica by seed, we gathered information about the year of seedling observation, the country, the geographical area, the locality name and the geographical coordinates where seedlings were found. When not reported, latitude and longitude of localities were indirectly estimated from an atlas. When seedlings were found in different sites (usually 10s of meters to kilometers apart) within the same locality, the name of the sites was reported when available. When seedlings were observed on different substrate types or depths within the same site, the observations were considered as a unique recruitment record. In addition, we extracted data on the age of seedlings at the time of observation and the year of establishment, the duration of seedling observation, local environmental characteristics (coastal features, water depth, habitat and substrate type), proximity to established meadows, management status (no protection or protection) and anthropogenic pressure level at the recruitment locality. The level of pressure was considered to be moderate or high in proximity to fishing ports, urbanized or industrial areas, coasts with altered sedimentary/hydrologic regimes, river mouths or boat traffic, and low in protected marine areas or natural parks. Quantitative data on seedling abundance (mean number of seedlings m^-2) in a given locality at the time of observation where retrieved when possible. When seedlings were present in different sites in the same locality, the relative mean abundance data were reported. Since in some cases data on seedling abundance were presented as range, the geometric mean was calculated and retained as an individual record of abundance. However, different authors used different sampling designs, sizes, or methods for determining seedling density. For some localities only the number of seedlings collected for morphological analysis or the total number of seedlings counted was available. Data on rhizome branching or production of new shoots and evidence of biotic disturbances (i.e., grazing on seedlings by fishes or sea urchins) were also retrieved when available. The search parameters were summarized in Table 1. Data obtained from all reports and our own observations were used to construct a database (Supplementary Table S1).

From all reports, we determined the global frequency of recruitment as number of years in which at least one successful event has been recorded divided per total number of years since the first seedling record. For each locality, we calculated the total number of recorded events. The total number of sites with recruits in a given year was also determined and the intensity of recruitment for each recruitment year was expressed as total number of sites in which seedlings were observed in that year. The spatial extent of recruitment was determined as total number of sites covered by recruitment since the first seedling record. The different types of substrate where recruits were found were categorized in four classes (sandy substrate, rocky substrate, dead “matte” and seagrass bed) and the total number of occurrence on each habitat class was calculated by combing data from all sites and years. When seedlings were found in the same habitat within the same site but in different years, the observations were considered as separate records. As seedlings were often present at different depths in the same site, the minimum depth (upper limit) and the maximum depth (lower limit) reached by seedlings were extracted from available data and the relative distribution frequencies analyzed to determine the average depth range of distribution of seedlings.

From available data on the abundance of seedlings at the time of observation we derived the overall mean of seedling abundance. When seedlings abundance data were available for different sites or substrate areas in a given locality, the mean seedling abundance for that locality was calculated by pooling data from the different sites or substrate areas. As the first year is considered the most critical for P. oceanica seedlings (Balestri et al., 1998a,b), for the purposes of this study, we considered well-established seedlings to be only those seedlings >1 year in age. To determine the chance of colonization success we thus selected those studies that monitored the fate of seedlings for at least 1 year or those that documented the presence of seedlings at least 1 year old. The total number of observations that documented the persistence of at least one seedling for more than 1 year (success) or the death/loss of all established seedlings (failure) in a given habitat type (sand vs. rock vs. dead “matte” vs. seagrass bed) and depth class (shallow vs. deep) was also determined and the relative frequencies of success/failure calculated by pooling data from all sites and years. As the type of substrate (rock vs. sand) and depth have been regarded as the main drivers of recruitment success at local scale (Piazzi et al., 1999; Badalamenti et al., 2015), the number of successes recorded for each substrate class (rock vs. sand) irrespective of depth, and for each depth class (shallow vs. deep) irrespective of substrate, was analyzed by Fisher exact p-test. Since only a few observations for seedlings on dead matte (4) and seagrass bed (1) were available, the relative number of success in these habitats were not analyzed.

Seedlings of P. oceanica observed in the Gulf of Saint Florent in July 2016 showed a dark seed coat still attached to the base of rhizome and the total number of leaves plus leaf scars produced by seedlings (20.3 ± 1.6 SE) was similar to that previously recorded in seedlings (22) maintained in culture for about 2 years (Caye, 1989), suggesting that they were approximately 2 years old, and thus established in the summer 2004. In one of the two selected sites, seedlings colonized an area of about 300 m² (mean seedling density, 22.0 ± 1.7 m^-2 SE) of rocky substrate covered by macro-algae, at 0.5–1.5 m depth, in proximity to the upper limit of a P. oceanica meadow. In the other site, isolated seedlings (1 seedling m^-2) were established on sandy patches within a Cymodocea nodosa (Ucria) Ascherson bed, at 0.5–1.5 m depth. The seedlings observed in the Gulf of Ventilegne in July 2016 (Figure 2) were very young (<1 year) and established in the same two sites where seedlings were found in 2005. In one of these sites, newly established seedlings were located on sandy patches at a depth of 0.5–2 m (mean seedling density, 42 ± 7 m^-2), while in the other one they were present both on sandy patches (mean seedling density, 8.1 ± 1.3 m^-2) and on rock (mean seedling density 9.3 ± 2.6 m^-2) at 0.4–2 m depth. Many seedlings established in 2016 were close (centimeters apart) to young plants established by seed in 2004 (Figure 2). Patches of seedlings (mean seedling density, 31.3 ± 7.4 m^-2) were also found into rocky pools at very shallow depth, 0.10–0.20 m depth (Figure 2). Seedlings on the aboral surface of the body of sea urchins, Paracentrotus lividus (Lamark), were observed (Figure 2). Seedlings found at Tonnara (Gulf of Ventilegne) in July 2016 were also very young (<1 year) and established at very shallow depth (0.10–0.20 cm) on rocky substrate colonized by macro-algae. Only one seedling per m² was found in this site (1 seedling m^-2).

All seedling patches marked on sand in 2005 in the site of Ventilegne were still present in July 2016, but they showed a substantial change both in their form and structure. Many seedlings, especially those initially situated in the central area of the patches, had disappeared (Figure 2) and this loss estimated in terms of percent cover accounted for 75% (± 2.88) of the original patch size. However, the loss on sandy patches was compensated by the growth of horizontal rhizomes and production of new shoots in surviving seedlings at patch edges (Figure 2). Instead, only 1 seedling per patch survived on rock and the young plants generated from survived seedlings showed up to three shoots at the time of observation (July 2016).

The first record of naturally established P. oceanica seedlings was reported in the 1987. Since this record, twenty-two citations in the scientific literature and gray literature, including personal communications from other authors and our own data, reported the presence of seedlings (Figure 3 and Supplementary Table S1). Five of these citations documented the presence of seedlings floating or stranded on beaches. Four out the remaining citations did not provide an indication of water depth and/or substrate type at the recruitment site, and one reference did not specify the year of seedling establishment. Only seven of the total records of in situ seedlings have been published in international peer-reviewed journals. Recruitment events have been recorded in 18 localities from four countries, Italy, France, Croatia, and Spain (Figure 1 and Supplementary Table S1). The latitudinal range of seedling distribution covered a relatively large band, from 37°39′ to 43°58′ N (Figure 1). In the Eastern Mediterranean basin, recruitment was observed only in one locality of the Central Adriatic Sea region (Dugi Otok Island, Croatia), and this was the northern extreme of the seedling distribution. The remaining events were recorded in the Western Basin; in the Balearic Sea to Tyrrhenian Sea (15 locations), and Gulf of Lyon and Ligurian Sea (three locations) regions. The southern extreme of the seedling distribution was in the Tyrrhenian Sea, Capo Feto (Sicily Island; Italy). Stranded seedlings were observed in eight localities of the Western Mediterranean and in one locality of the Eastern Mediterranean (Ionian Sea), providing evidence of a potential recruitment event in the neighborhood, but they were excluded from the analysis. In six localities (Favignana, Ustica, Gulf of Ventilegne, Gulf of Saint Florent, Livorno, and Mallorca), seedlings were found in different sites, and in total thirty sites had at least one recruitment event (Figures 1, 3 and Supplementary Table S1). From 1986 and 2016, the presence of new recruits was noticed 10 of the years (Figure 3), corresponding to a frequency of about 0.33 events y^-1, and at least one recruitment event was observed every year from 1994 to 1998. The mean number of sites colonized every year was 1.03 (± 0.04 SE), and in those years in which at least one recruitment event was observed, the number of colonized sites varied from 1 to 12 (mean, 3.20 ± 1.11 SE). The higher intensities of recruitment (Figure 3) were recorded in 1994 (five localities, six sites in total,) and 2004 (eight localities, 12 sites in total). Two recruitment events each at Ustica Island (in 1997 and 2009), Livorno (in 1994 and 2004) and Gulf of Ventilegne (in 2004 and 2016), and three events at Favignana Island (in 1994, 1995, and 2004; Supplementary Table S1) have been recorded.

Most localities (72%) where seedlings were found are situated along the coasts of islands (Supplementary Table S1). The presence of recruits along continental coasts was reported only in five localities, Gulf of Giens, Gulf of Juan, Livorno, Rosignano Solvay, and Follonica. Seven localities were characterized by moderate or high levels of anthropogenic pressure, while the remaining ones were located in zones with low levels of pressure such as marine protected areas and marine parks. Seedlings colonized mainly sheltered sites usually along curvilinear coasts such as bays and gulfs, or small inlets. Only three localities were situated in relatively exposed sites, Rosignano Solvay, Livorno, and Capo Feto. In all recruitment sites, seedlings were close to established meadows. Seedlings were found in previously unoccupied areas colonized by macro-algae, except that in three localities (Follonica, Rosignano Solvay and Livorno, Italy) where they were recruited within dead “matte” areas in disturbed meadows, and in one locality (Saint. Florent, Corsica), in which they were present in a C. nodosa bed (Supplementary Table S1). Established seedlings were also found in rocky pools in two localities, Gulf of Ventilegne (Corsica) and Pantelleria Island (Italy). In five of the 18 localities seedlings were present on two different types of substrate, sand and rock or sand and dead “matte” (Supplementary Table S1). The total number of occurrences of seedlings on rocky habitats was about twofold more than that on sandy habitats (Figure 3). Seedlings were found at different depths, from 0 to 15 m, but in only two locations did they reach depths below 10 m (Figure 3 and Supplementary Table S1). The mean minimum depth of seedling distribution did not exceed 2 m (mean, 1.9 ± 0.5 m, median depth limit 1 m), while the mean maximum depth was above 5 m (mean 4.9 ± 0.89, median depth limit 3 m). Seedlings colonizing sandy substrates and dead “matte” were generally located deeper (2.9 ± 0.8–6.0 ± 1.24 than those on rock (0.9 ± 0.22–4.2 ± 1.03) or in C. nodosa beds (0.5–1.5 m). The deeper seedlings were observed on dead “matte” (5.6 ± 2.33–10 m). Data on seedling abundance were available for nine localities (Supplementary Table S1). Mean seedling density recorded in 2004 in the Gulf of Ventilegne (135.2 ± 24.3 m^-2) was more than fourfold the average seedling density of all localities (20.7 ± 12.9 m^-2).

In five localities seedlings were 1 or 2 years-old at the time of observation and hence they had survived the most critical life period. In six localities, established seedlings were monitored over time but the duration of the observational period was limited (<3 years). Only in one locality, Gulf of Ventilegne, did the observational period exceed 3 years (11 years, present study). The establishment of seedlings was successful in all monitored localities and sites as at least one seedling was still present at the end of the monitoring period. Overall, the chance of colonization success on rocky substrate was significantly higher, about twofold more than on sandy substrate (Table 2) irrespective of depth (p = 0.008). The probability of success for seedlings on dead “matte” and C. nodosa beds was 100% (Table 2) but too few observations were available to infer meaningful conclusions about the recruitment success of seedlings in these habitats. No difference was detected between shallow and deep depth classes (p = 0.56). Four studies reported the production of at least one new rhizome ramification (Supplementary Table S1) and only the present study documented the expansion of seedling patches. Clear evidence of damage on seedlings by herbivores was never observed (Supplementary Table S1).

Our long-term field observations of seedlings established in the Gulf of Ventilegne in 2005 allowed us to document the formation of patches by seeds and their evolution over their first decade, demonstrating that under particularly favorable conditions seedlings may persist and successfully colonize sandy substrates even at very shallow depths. The slow rate of expansion of these patches (10s of centimeters in 11 years) is in agreement with the prediction of simulation models which indicate that a new clone of P. oceanica may take 100 years to attain a diameter of 8 m (Kendrick et al., 2005). A previous analysis of the initial spatial distribution of seedlings at Ventilegne has shown an aggregated pattern with higher seedling density closest to the center of seedling patches and lower densities at increasing distance from the center (Balestri and Lardicci, 2008). A positive relationship between seedling density and mortality rate in the post-establishment phase also emerged from the previous study (Balestri and Lardicci, 2008). Here, the formation of gaps from mortality inside seedling patches supports the hypothesis that competition for limiting nutrients or available space occurred among some seedlings as they increased in size due to overcrowding. But, a change in the topography of sea floor due to physical disturbance, in particular the formation of erosion channels created by elevated levels of turbulence within the patches during severe storms, might have played a role. Even though high herbivore consumption rates of fruits/seeds have been reported (Balestri and Cinelli, 2003) and bite marks on leaves were found on transplanted seedlings of P. oceanica (Domínguez et al., 2012), herbivore pressure did not appear to be a threat for early life stages. However, our observations revealed that the sea urchin P. lividus, one of the major consumers of P. oceanica fruits, may cover itself with detached seedlings. Further studies would be necessary to establish whether, and if so to what extent, this cryptic covering behavior removing seedlings from rocky substrate, may reduce the success of establishment.

Previous studies have shown that P. oceanica meadows have flowered on average every 5 years over the Mediterranean Sea in the last three decades (Diaz-Almela et al., 2007). Our analysis revealed that at least one recruitment event has occurred approximately every 3 years since the first seedling record in 1986. Clearly, this is a conservative estimate likely underestimating the actual frequency of recruitment, being based on occasional records rather than on systematic research. Only one recruitment locality (Dugi Otok Island, Croatia) was in the Eastern Mediterranean, and the remaining localities (17) were in the Western Mediterranean. This distribution might reflect either an unequal investment in research with a high density of observational efforts concentrated in the western sector and a paucity of studies on the eastern sector of the basin, or a different flowering frequency/intensity of meadows in the two sectors (Diaz-Almela et al., 2007), or a combination of both. The higher intensities of recruitment events, in terms of number of colonized sites, followed the massive flowerings of 1993 and 2003 (Diaz-Almela et al., 2006; Sghaier et al., 2014). This observation supports the hypothesis that not only the reproductive output, but also the reproductive success of P. oceanica, has increased, probably in response to changing environmental conditions. More importantly, the repeated recruitment events recorded in four localities of the Western Mediterranean, Island of Favignana, Island of Ustica, Gulf of Ventilegne and Livorno, demonstrate the existence of areas particularly favorable to the establishment of seedling populations. The first two localities are located along the Sicilian coasts, in the center of a biogeographic transition zone separating the western and eastern Mediterranean basins (Bianchi, 2007). Studies have shown that many meadows present along these coasts have flowered almost every year from 1978 to 2005 and produced large amounts of seeds (Calvo et al., 2010). Past studies suggested that the warmer south Mediterranean waters of Sicily are the best environment for P. oceanica flowering and growth, while the winter seawater temperatures of the northwestern Mediterranean are below the optimum for flowering induction (Molinier and Picard, 1952; Semroud, 1993). However, recent studies indicated that temperature variation rather than mean value could be the main trigger of flowering (Diaz-Almela et al., 2007). Since the genetic diversity of some meadows in the biogeographic transition zone appears be higher compared to others meadows of the Mediterranean (Jahnke et al., 2015), future studies should investigate whether there is a relationship between the success of seed production in these meadows and their genetic diversity. Flowering had rarely been observed before 1984 along the coasts of Corsica and Livorno (Caye and Meinesz, 1984), but from 1994 onward this phenomenon occurred regularly (Balestri, 2004; Gobert et al., 2005), possibly due to moderate warming of the northwestern Mediterranean over the past decades (Lejeusne et al., 2010; Marbà et al., 2015). Given the extremely high number of seedlings recruited in the Gulf of Ventilegne (up to 480 seedlings m^-2, Balestri and Lardicci, 2008) and their persistence and growth, this site presently has a high prospect for supporting the development of newly established clones in the future. Cleary, a systematic longer-term monitoring of recruitment sites is needed to confirm the hypothesis.

The presence of recruits established on new unoccupied substrate areas at very shallow depths supports the hypothesis that sexual recruitment within established meadows is a highly improbable event for P. oceanica accordingly to the initial seedling recruitment model (Arnaud-Haond et al., 2014). The finding of seedlings mainly in sheltered shallow sites suggests that coastal morphology and in particular the presence of wave-sheltered inlets, such as bays and gulfs, along the fruit dispersal trajectory could play a key role in determining the initial distribution of seedlings, capturing and retaining most floating fruits until seed release. A similar apparent “preference” for sheltered shallow sites has been reported for the congeneric Australian species, Posidonia australis Hook. f. (Meehan and West, 2004). The presence of P. oceanica seedlings at shallow (0–3 m) depth indicates that neither photo-damage nor high hydrodynamic forces and temperatures generally associated with shallow depths may affect seedling establishment, at least its initial stages. Previous studies have shown that a low light environment is more favorable to P. oceanica growth than a high light one, and that plants growing in the upper stands of meadows (<5 m depth) are under stressful light conditions, but physiologically adapted to these conditions and genetically differentiated from those living in deeper stands (Dattolo et al., 2014). However, other studies have found that seedlings require an environment with relatively higher light compared with adults, an adaptation strategy to survive the oligotrophic conditions of the Mediterranean (Celdrán and Marín, 2013). This strategy could explain the presence of seedlings in very shallow areas as well as their apparent absence at greater depths or inside well-established stands. On the other hand, at shallow depths near-bottom orbital velocities are too high also for adult shoot establishment except in very sheltered conditions (Infantes et al., 2009). As seedlings have been found to be vulnerable to physical perturbations related to wave and currents (Infantes et al., 2011), prolonged periods of calm sea conditions could be required for the establishment of seedlings at shallow depths. Historically, P. oceanica has been considered a species that grows preferably on sandy habitats, although a recent study (Montefalcone et al., 2016) has shown the presence of meadows developed on rocks at very shallow depths (1.5 m depth), outside the theoretical reference zone for the meadow upper limit (>5 m depth) predicted by models (Vacchi et al., 2014). The capacity of seedlings to establish on both rocky and sandy substrates could be linked to the plasticity of the root system (Balestri et al., 2015) and to the production of adhesive root hairs on rocky substrate in the early phase of their development (Badalamenti et al., 2015). But other factors, such as the presence of algal vegetation and fissures on rocky substrates, could also play a role facilitating seedling anchorage (Alagna et al., 2013; Balestri et al., 2015). However, previous studies reported higher mortality rates of seedlings on sandy patches than on rock during their first 2–3 years. This is probably because the spatial extension of the root system of seedlings is not enough to counteract hydrodynamic forces generated by stronger storms at shallow depths on unstable substrates. Results of our analysis showed that the chance of survival and formation of new clones was effectively lower for seedlings established on sandy habitats than those on rocky ones irrespective of depth, reinforcing the hypothesis that substrate stability or complexity could ultimately determine the colonization success of the species (Balestri et al., 1998b; Badalamenti et al., 2015).

The ability of seedlings of P. oceanica to grow and establish new patches outside the upper limit of extant meadows and the recurrent occurrence of sexual reproductive events highlight the importance of developing additional management measures to improve the effectiveness of habitat/species conservation in the future. Such measures could include, for example, actions for the protection of those meadows that flower more profusely to ensure the conditions required for the development and ripening of seeds, as well as the development of programs specifically designed to identify, monitor and protect new recruitment localities. In fact, multiple strategies have been attempted in many European countries to preserve P. oceanica meadows in the face of predicted climate-induced alterations. However, monitoring programs have focused on well-established meadows and most monitoring stations are currently located in the shallow- or mid depth of meadows, usually below 5 m of depth (Montefalcone, 2009; Boudouresque et al., 2012), thus outside the present range of distribution of established seedlings. Moreover, some conservation efforts have attempted to improve coastal seawater quality and remove disturbances that have caused or will potentially lead to the decline of existing meadows (EU Water Framework Directive, WFD, 2000/60/EEC, Marine Strategy Framework Directive MSFD, 2008/56/EEC). The rationale governing these efforts is to maintain the environmental services provided by meadows, which are directly or indirectly related to surface and cover of well-established meadows. However, populations of long-lived species dominated by a few old clones, such as P. oceanica, may persist despite suboptimal site conditions, and thus their patch occupancy pattern may not be in equilibrium with the present landscape configuration but rather reflect the historical landscape (Eriksson, 1994). Even occasional inputs of new genets may increase the probability of adaptation-capacity of species to changing environmental conditions (Ehlers et al., 2008; Hughes and Stachowicz, 2009).

Projections indicate that the sea level in Mediterranean will rise over 30–60 cm in the next century (IPCC, 2007). For example, in Corsica, the mean sea level has risen by 18 cm between 1870 and 2000, including 6 cm over the past 20 years, causing the regression of some P. oceanica meadows near the depth of compensation of the species and in sectors where the slope is relatively slight (Pergent et al., 2015). Since the prevalent trajectory of colonization of the seedlings in Corsica appears to be toward the coastline, predicted sea level rise could alleviate environmental stresses (physical disturbances, photo-damage, and temperature fluctuations) experienced by surviving seedlings, and provide an opportunity for the species to move landward and colonize newly submerged areas. Moreover, results or recent laboratory studies suggested that projected increases in pC0 ₂ concentrations could have positive effects on seedlings by increasing their photosynthetic performance and carbon fixation activity during the initial phases of development, enabling them to better resist or recover from stressful conditions, like adverse temperature and light conditions (Hernán et al., 2016). However, stronger storms, anthropogenic pressure, coastal activities and presence of physical barriers in the vicinity of recruitment sites, could be important threats for seedlings. Fortunately, many recruits such as those observed in Corsica were located inside the boundaries of marine protected areas or national parks. Nevertheless, damage to established meadows due to recreational activities (fishing, boat anchoring, sewage effluents or organic inputs from visitors) has been reported in some protected areas (Marbà et al., 2002; Bonacorsi et al., 2013). More restrictive measures would therefore be necessary to reduce the potential impact of such activities on seedlings, in order to facilitate their expansion on new available sites. In exposed sites, it could also be necessary to use anchoring and protective structures for seedlings to reduce the risk of plant dislodgment during storms as well as to prevent overgrowth of out-competing macro-algae.

Seedlings are increasingly an important management tool for seagrass restoration, and studies have shown that cultivated seedlings of P. oceanica can be transplanted in the field with relatively high success and thus used as planting material for assisted colonization at shallow sites or for restoration of small damaged areas in disturbed meadows (Balestri et al., 1998b; Domínguez et al., 2012; Terrados et al., 2013). Since stranded P. oceanica fruits are increasingly available in many countries, they may be planted in selected suitable areas to create reservoirs of juveniles for future restoration activities. Temporary nurseries could be also created into aquaculture facilities for the duration of restoration programs (Balestri and Lardicci, 2012; Leal et al., 2016). The harvesting of seedlings in natural recruitment sites and their translocation into distant recipient sites should be not encouraged.