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Do we protect freshwater eels or do we drive them to extinction?
SpringerPlus volume 3, Article number: 534 (2014)
Freshwater eels are important animals because they have a unique catadromous life history and are used as food resources. European, American and Japanese eel populations now are considered to be outside the safe biological limits and are seriously threatened with extinction. Therefore, the European eel was recently categorised as critically endangered by the European Union and the United Nations. One of the reasons for the drastic decline in eel populations is overfishing, which has caused a high demand for eel aquaculture; eel aquaculture completely depends on wild juveniles, and in contrast to animals, artificial propagation has not yet succeeded for the eels. Therefore, commercial eel industries are now considering tropical eels as possible replacement for European and Japanese eels to compensate for declining stocks. In this study, I attempt to examine the present status of the biology and stock of tropical eels. However, useful scientific research and information on the biology and stock assessments of tropical eels are lacking, a situation quite different from that for other temperate freshwater eels, which have been well studied for several decades with trends and recruitment patterns being on record. Nevertheless, the present tropical eel catch has been reported as being less than half that of 20 years ago. The present trends in eel stocks and utilization for human consumption suggest that all eel populations will decline to numbers that fall outside safe biological limits and will be seriously threatened with extinction without protection and conservation from strict enforcement of local and international laws.
Freshwater eels are exotic animals, and despite a huge number of scientific studies conducted with eels, crucial aspects of their biology remain a mystery. No one has yet observed eels spawning in the natural environment, as spawning areas are located in the open ocean. This distinctly contrasts with other animals, such as anadromous salmon fish whose biology is well studied and better understood because localized spawning stocks are relatively easy to survey when the adults return to freshwater for spawning. Nineteen species of freshwater eels have been reported worldwide, 13 from tropical regions. Of the latter, seven species occur in the western Pacific around Indonesia (Ege 1939; Castle and Williamson 1974; Arai et al. 1999). Molecular phylogenetic researches on freshwater eels have recently revealed that tropical eels are the most basal species originating in the Indonesian region and that freshwater eels radiated out from the tropics to colonise the temperate regions (Minegishi et al. 2005). Tropical freshwater eels must be more closely related to the ancestral form than are their temperate counterparts.
Freshwater eels are the most important of the eel families from a conservation standpoint because they have a unique catadromous life history and are used as food resources. Recently, however, juvenile abundance has declined dramatically: by 99% for the European eel and by 80% for the Japanese eel (Dekker et al. 2003). Recruitment of the American eel near the species’ northern limit has virtually ceased (Dekker et al. 2003). Other eel species, including Australian and New Zealand eels (Anguilla dieffenbachii and A. australis), also show indications of decline (Dekker et al. 2003). The main problem is that all young eels used in cultivation are wild juveniles (glass eels and elvers), which are captured in estuaries. Almost all (90%) of the total world eel supply comes from aquaculture FAO (Food and Agriculture Organization of the United Nations) (2010). Therefore, the supply of eel resources for human consumption is completely dependent on wild catch.
The population size of wild European eel juveniles has linearly decreased from over 200 tonnes in the early 1960s to 20 tonnes at present, and in Japanese eels, a shortage of fry has become a serious problem for fish culture in recent years (Arai 2014a). Eel stocks throughout Europe are also declining (Dekker 2003a), and eel fishery yields have decreased in most European countries. The populations of the European, American and Japanese eels are considered to be outside safe biological limits, and current fisheries are not sustainable (Dekker 2003b; Dekker et al. 2003; Arai 2014a). The European eel was recently categorised as critically endangered by the European Union (EU) and the United Nations (CITES 2007), although other eels have not yet seriously been considered for protection. Since the early 1980s, juvenile recruitment has decreased, dropping to 1% of the levels encountered in the 1970s.
The causes of decline in stock and recruitment are not well understood. Overfishing, habitat loss and migration barriers, increased natural predation, parasitism, ocean climate variation, and pollution might have an impact (Knights 2003; Friedland et al. 2007; Bonhommeau et al. 2008; Marcogliese and Casselman 2009). Since the European eel was listed by CITES under Appendix II and came under protection in March 2009, and since the export/import ban was issued by the EU in 2010, the international trade of juvenile eels has changed. Most recently, the Japanese eel was added to the IUCN’s list with an endangered classification (IUCN 2014), suggesting it has a high risk of extinction. Species other than European and Japanese eels, including several tropical species, seem to have replaced the European eel on the international market. In addition, countries including Canada, the USA, the Dominican Republic, Morocco, Madagascar, the Philippines and Indonesia have now entered the market and supply juvenile eels for the farming industry in China, Japan, Taiwan and South Korea (Crook and Nakamura 2013; Anonymous 2013a, Anonymous 2014). However, fewer studies are available on tropical eels than for European, American, Japanese, Australian and New Zealand eels. The lack of availability of basic life history, stock and population information on the tropical eels could lead to further serious declines in these eels. Before tropical eel juveniles are used to replace and augment European and Japanese eels stocks, stock assessments and recruitment studies of source stocks are needed to determine the sustainability of tropical eels. However, consumers in East Asian countries do not pay attention to protection, conservation and enhancement of tropical eel populations, concentrating instead on having a stable eel supply and trade as they did with European and Japanese eels. If we continue such ad hoc eel resource usage, eels will become extinct around the world in the near future. Due to artificially induced breeding techniques for eel populations that are not yet firmly established, unlike populations of salmon, blue fin tuna and livestock, such a status will accelerate from threatened to declining wild eel stocks.
In this paper, I review the present status of recruitment and stocks of tropical eels. There is a clear lack of historical data regarding stock and recruitment of tropical eels. This lack of scientific research, assessment and protection will lead to the collapse of tropical eel populations and affect the maintenance of European, American, Japanese, Australian and New Zealand eels. Rapid stock assessment and continuous monitoring for recruitment in tropical eels are needed before usage of this resource to avoid eel extinctions around the world.
Present status of trading in tropical freshwater eels
The present target tropical eel is Anguilla bicolor from Indonesia and the Philippines (Anonymous 2013a, Anonymous 2014). China, Japan, Taiwan and South Korea have imported cultured and sold the eel to consumers, using it to replace and compensate for declining European and Japanese eel sources. Although Indonesia and the Philippines prohibit the export of juvenile eels less than 150 g in weight from Indonesia and less than 15 cm in length from the Philippines to protect their resources, no regulations are enforced for juvenile fisheries in these countries (Anonymous 2012a, Anonymous 2012b). All marked eels are either wild-caught eels or cultured eels that were wild juveniles. No historical stock or juvenile recruitment data for eels are available in these countries; therefore, the fluctuation in the abundance of eels is not well understood.
Present status of biological studies in tropical glass eels
The only available data in tropical eels show the trend for recruitment for three years from 1997 to 1999 from quantitative sampling from an estuary in Indonesia (Arai et al. 1999; Sugeha et al. 2001). Juveniles were found to occur throughout each year (Figure 1), with the highest recruitment occurring at the time of the new moon (Sugeha et al. 2001). Although year-round recruitment in tropical freshwater eels was found in other regions such as Philippines (Tabeta et al. 1976), Australia (Shen and Tzeng 2007) and Taiwan (Leander et al. 2012), quantitative surveys adjusting moon phase or other ambient environmental parameters did not conduct in those studies. Thus, it seems to be impossible to understand the fluctuation of glass eel abundance exactly.
More than 30,000 glass eels were collected quantitatively in the Poigar River estuary on north Sulawesi Island, Indonesia, in monthly collections from 1997 to 1999 (Arai et al. 1999; Sugeha et al. 2001). The specimens were identified three species, Anguilla celebesensis, A. marmorata, and A. bicolor pacifica, were found each year in fluctuating abundances (Figure 2). A. celebesensis was the most abundant species and comprised 73.5%, 79.5%, and 81.9% of all glass eels recruiting to the estuary of the Poigar River in 1997, 1998, and 1999, respectively (Figure 2) (Arai et al. 1999; Sugeha et al. 2001). This species was relatively abundant in all three years with peaks during June in 1997 and 1998 and during September in 1999 (Figure 2). A. marmorata was the second most abundant species and comprised 23.8%, 18.8%, and 17.7% of the yearly catches, respectively, and reached peaks in abundance during June in 1997 and 1998, and during January in 1999 (Figure 2). A. bicolor pacifica comprised only 2.7%, 1.7%, and 0.3% of the yearly catches respectively, with peak catches in June in 1997, in January in 1998, and in January and February in 1999 (Figure 2). A. celebesensis and A. marmorata were collected almost throughout the year in 1997, 1998, and 1999, suggesting that in contrast to the temperate eels that recruit during half the year from winter to spring, these tropical eel species recruit to some degree throughout the year.
The temporal patterns of glass eels catches near the mouth of the Poigar River differed among species and years suggesting that there was considerable inter-annual variation in the recruitment patterns of glass eels in the region. However, such systematic surveys for tropical glass eels have never been conducted in other tropical regions. Further long-term surveys should be urgently needed to understand natural (e.g. ambient environments such as global climate change and oceanic transportation systems) and anthropogenic impacts (e.g. overexploitation, habitat degradation and pollution) on the recruitment of glass eels in tropical regions.
Recruitment mechanisms of tropical freshwater eels
Glass eel catches in Japan has indicated that the catches decreased in association with El Niño events (Kimura et al. 2001). This suggests that the location of the spawning area changed with the appearance of El Niño. The salinity front functions are believed to be as a landmark for spawning migration of the Japanese eel (Kimura and Tsukamoto 2006). Indeed, many leptocephali have been distributed near the salinity front (Kimura et al. 1994, Tsukamoto et al. 2003). Associated with the El Niño events, salinity front moves considerably leading to change the leptocephali transportation route. The winter from December 1997 to February 1998 was recorded as great El Niño event, i.e. the period was the second warmest and seventh wettest since 1895 (Ross et al. 1998). If the spawning areas of tropical eels recruited to North Sulawesi move associated with movement of the salinity front around their spawning areas, transportation systems of tropical eel leptocephali might be also changed and the event lead to the low catch of glass eels in the estuary of the Poigar River. The spawning area of A. marmorata in the Poigar belonging to the North Pacific population (Minegishi et al. 2008) could be located in the western North Pacific where is the spawning ground of the Japanese eel A. japonica (Tsukamoto et al. 2011, Figure 1). Recently, one spawning-condition female A. marmorata was collected corresponded to the estimated spawning area in A. marmorata by Arai et al. (2002) as determined by otolith analyses. Thus, leptocephali of A. marmorata might be affected on the El Niño event in the winter between 1997 and 1998 in the western North Pacific. These results suggest the considerably low catch of glass eels in the Poigar River in 1998 in A. marmorata and similar declining of glass eels would be also found in A. celebesensis and A. bicolor pacifica in the year caused changes of transportation systems from their spawning grounds to growth habitats (Figures 1 and 2) due to passive transportation by oceanic currents from their spawning sites.
Although a few tropical glass eels recruited year round, temperate anguillid species showed much shorter seasonal ranges in recruitment period. In the northern hemisphere, A. japonica glass eels recruit to the east coast of Japan from October to May (Matsui 1952), the west coast of southern Japan from January to June (Kawakami et al. 1999) and the east coast of central Japan from November to June (Aoyama et al. 2012). For the Atlantic temperate eels, the peak in recruitment of A. rostrata has been reported to be in April and May (Haro and Krueger 1988), and the recruitment season of A. anguilla was from late November to early July, with the peak of upstream migration into freshwater in February and May (Gandolfi et al. 1984). In the southern hemisphere, on several streams in eastern Tasmania, the glass eels of A. australis were collected at the first riffle during all seasons of the year except mid summer with peak in October, and during late summer and autumn for the more tropical A. reinhardtii glass eels with peak in April (Sloane 1984). Jellyman (1977) found that the invasion by both New Zealand species into the Makara Stream commenced in July, with that of the long-finned eel A. dieffenbachii finishing by November with peaks in August and September, and that of the short-finned eel A. australis schmidtii finishing by December with peaks in September and October. This was similar to the seasonal migration of both species in the Waikato River, New Zealand, where the main migratory period extended from August to October (Jellyman 1979). These results suggest that tropical glass eels tend to recruit throughout the year while most temperate species recruit during about half of the year or less.
Analyses of the otolith microstructure showed that the ages at recruitment of tropical eels were constant throughout the year (Arai et al. 2001). The spawning seasons of tropical eels were found to extend throughout the year (Arai et al. 2001). The year-round spawning of tropical species and constant larval growth throughout the year extend the period of recruitment to estuarine habitats to year-round in tropical eels. Local short-distant migration made by tropical eels (Arai 2014b, Figure 3) enables such spawning ecology and recruitment mechanisms. For temperate eels, the retention of their spawning areas in the tropics would require that the eels migrate thousands of kilometres to have clearly seasonal patterns of downstream migration, spawning in the open ocean, and recruitment of glass eels.
Present status of stocks in temperate freshwater eels
In contrast to the tropical eels, historical stock data for wild eels are available for European, American, Japanese, Australian and New Zealand eels. For European and Japanese eels, wild catches fell gradually after the peak levels of the late 1970s and early 1980s in accordance with the increasing demand for eels in aquaculture (Figure 4). Trends in juvenile abundance of the major eel stocks for European, American and Japanese eels also suggest that juvenile populations have declined dramatically and clearly lie outside of safe biological limits (Figure 5). Recruitment of European and Japanese eels in each distribution range declined by 99% and 80%, respectively. Recruitment of American eel at the northern limit of its distribution has ceased (Figure 5).
Worldwide decline of freshwater eel populations
The worldwide decline of freshwater eel populations is a major concern for animal conservation and diversity. European, American and Japanese eels have experienced sharp declines across their ranges over the last 30–40 years (ICES 2006; Aprahamian et al. 2007; Castonguay et al. 1994; Dekker et al. 2003, 2007) (Figures 4 and 5). In spite of the seriousness of the situation for juvenile eel recruitment, eel consumption is still increasing. To continue to supply large amounts of eels to consumers, the replacement and compensation have started to import eels from foreign countries, mainly the Philippines, Indonesia and Madagascar (Anonymous 2013a, [b], 2014). The main problem with consumption of this animal is that artificial propagation has not yet succeeded as it has with other common animals, such as salmon, blue fin tuna and livestock; therefore, juvenile eels are high-value aquaculture commodities that put high fishing pressure on a natural environment. Almost all (90%) of the world’s eel supply comes from aquaculture FAO (Food and Agriculture Organization of the United Nations) (2010) and the present eel aquaculture completely (100%) depends on wild juveniles. More than 90% of the world production of eels is cultured in East Asia, primarily Japan, Taiwan and China (Ringuet et al. 2002). Thus, wild juvenile eel catch will be needed in the future for these countries due to the increasing demands of aquaculture (Figure 4). To enhance natural eel stocks and continue their commercial usage for human consumption, studies related to the establishment of commercial juvenile production are urgently required and should focus on this goal as a means of protecting wild eel stocks.
Lack of stock assessment and stock enhancement in freshwater eels
For the European eel, as a consequence of these concerns, the European Commission has agreed to an eel recovery plan, the aim of which is to return the European eel stock to sustainable levels of adult abundance and juvenile recruitment (Svedäng and Gipperth 2012). In 2007, the European eel was listed in Appendix II of CITES (the Convention on International Trade in Endangered Species of Wild Fauna and Flora) and Appendix II “includes species not necessarily threatened with extinction, but in which trade must be controlled to avoid utilization incompatible with their survival” (CITES 2007). Although stock assessment and management of the European eel have received increasing attention from both the scientific community and fisheries agencies in recent years (ICES 2006), such assessment and management of the Japanese eel have not yet been well studied. Such studies would help with the development of a concrete conservation policy and management applications for stock enhancement. Please note that despite the high demand for the product, the peak capture of Japanese eels is less than the lowest captures of European eels (Halpin 2007, Arai 2014a) (Figure 4). This fact indicates a relatively low virgin biomass of Japanese eels. To make matters worse, trade in tropical eels started with no scientific assessment and management before usage in spite of our experience with severely declining stocks in European, American, Japanese, Australian and New Zealand eels. Until now, there has been no information available on historical fishing records in tropical eels and only limited biological information compared with European, American, Japanese, Australian and New Zealand eels.
For marine species, dispersal during the larval phase is often important in shaping population genetic structure, and ocean currents play an important role in larval transport (Sponaugle et al. 2002; Fisher 2005). The migration distances for temperate eels such as the Atlantic and Japanese eels show thousands of km, while those of the tropical eels have been found local-short distance migration less than 100 km (Arai 2014b). The larval dispersal times for temperate eels such as the Atlantic, Australian, Japanese and New Zealand eels were 1 to 5 months longer than those of the tropical species (Arai et al. 2001). The time and distance required for dispersing larvae and migrating adults might be longer in temperate eels. The results suggest that higher genetic differentiation might be occurred in temperate species than that of tropical species.
Understanding the population structure of freshwater eels is the first step towards establishing management and conservation efforts for them. Most studies on the population genetic structure of anguillid eels have focused on the temperate species of A. japonica (Sang et al. 1994; Tseng et al. 2006; Han et al. 2008), A. rostrata (Avise et al. 1986; Wirth and Bernatchez 2003), A. anguilla (Lintas et al. 1998; Wirth and Bernatchez 2003; Dannewitz et al. 2005) and A. australis (Dijkstra and Jellyman 1999; Shen and Tzeng 2007). Several studies have examined the tropical species of A. marmorata, A. bicolor and A. bengalensis which have been found to have multiple populations or metapopulations throughout its wide range (Minegishi et al. 2008; Gagnaire et al. 2011; Donovan et al. 2012, Watanabe et al. 2014).
The Japanese eel shows spatial genetic differentiation throughout its range (Tseng et al. 2006), however Han et al. (2008) found that genetic differentiation is temporally stable at a single location. No apparent loss of genetic diversity and occurrence of a genetic bottleneck for the Japanese eel populations were found with estimating the effective population size (Ne) exceeded 500 (Han et al. 2008). In the European eel, highly significant genetic differentiation among inter-annual or among intra-annual arrival recruits was found (Pujolar et al. 2006), indicating variance in reproductive success (genetic patchiness). Because tropical eel species might have lower genetic differentiation made by local-short distance migration, loss of genetic diversity and occurrence of a genetic bottleneck would be occurred more frequently than those of temperate species. However, such evaluations have not been well examined in tropical species. Further molecular genetic study is needed for tropical eels and it would contribute to their sustainable management and conservation.
Do we drive freshwater eels to extinction?
Although European, American, Japanese, Australian and New Zealand eels appeared to have much shorter seasonal ranges during the recruitment period for about half of the year or less (Matsui 1952; Haro and Krueger 1988; Gandolfi et al. 1984; Sloane 1984; Jellyman 1977), at least a few juveniles of the tropical eels recruited year round. The temporal pattern of tropical juvenile recruitment was found to have considerable interannual variation (Arai et al. 1999; Sugeha et al. 2001) (Figures 1 and 2). Thus, continuous long-term research is needed to determine the causes of the variation. Such year-round recruitment in tropical eels might be more convenient in aquaculture, which would be able to culture eels throughout year. In fact, 70 tonnes of eels were exported to Japan from one eel farm in Indonesia in 2013, and this amount is estimated to double in 2014 (Anonymous 2014). Because the present market price of juvenile eels is 150 times higher than 20 years ago, a number of village people near juvenile eel fishing grounds in Indonesia tend to concentrate on eel fishing only, whereas they used to focus on farming and fishing (Anonymous 2014). However, the juvenile eel catch is now reported to be half that of 20 years ago (Anonymous 2014), although the estimated decline has never been evaluated based on scientific research. The causes of decline in eel stocks and recruitment are not well understood. One of the main reasons must be overfishing, as sharp declines in wild European and Japanese eel populations correspond to drastically increased aquaculture demands for these eels since the 1970s (Figure 4). Now, tropical eels may have begun to follow the same trends as the European and Japanese eels. This suggests that we cannot rule out overfishing in tropical countries. Thus, if the wild juvenile eel catch of tropical eels continues to increase without assessment and protection of the stock and regulation of the catchment, all eel populations will decline to numbers outside safe biological limits. Currently, European, American and Japanese eels are seriously threatened with extinction due to eel consumption (Figures 4 and 5), and demand is still increasing. After the stocks and recruitment collapse in the present target eel species and areas, we will have to seek other targets for replacement and compensation to continue eel consumption. We may not be able to see such a unique animal on the earth in the near future.
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I thank Dr. Willem Dekker for providing the original data published in Dekker et al. (2003) to show trends in juvenile stocks of the European, Japanese and American eels in Figure 5. This work was supported in part by the Ministry of Higher Education Malaysia under the Fundamental Research Grant Scheme (Vot No. 59281). The Higher Institution Centre of Excellence (HICoE) Research Grant (Vot No. 66928), under the Institute of Oceanography and Environment (INOS), also jointly supported this study.
The author declares that he has no competing interests.
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Arai, T. Do we protect freshwater eels or do we drive them to extinction?. SpringerPlus 3, 534 (2014). https://doi.org/10.1186/2193-1801-3-534
- Stock assessment
- Tropical eels