China is facing intense coastal eutrophication. Large-scale seaweed aquaculture in China is popular, now accounting for over 2/3’s of global production. Here, we estimate the nutrient removal capability of large-scale Chinese seaweed farms to determine its significance in mitigating eutrophication. We combined estimates of yield and nutrient concentration of Chinese seaweed aquaculture to quantify that one hectare of seaweed aquaculture removes the equivalent nutrient inputs entering 17.8 ha for nitrogen and 126.7 ha for phosphorus of Chinese coastal waters, respectively. Chinese seaweed aquaculture annually removes approximately 75,000 t nitrogen and 9,500 t phosphorus. Whereas removal of the total N inputs to Chinese coastal waters requires a seaweed farming area 17 times larger than the extant area, one and a half times more of the seaweed area would be able to remove close to 100% of the P inputs. With the current growth rate of seaweed aquaculture, we project this industry will remove 100% of the current phosphorus inputs to Chinese coastal waters by 2026. Hence, seaweed aquaculture already plays a hitherto unrealized role in mitigating coastal eutrophication, a role that may be greatly expanded with future growth of seaweed aquaculture.
High population density, intensive agriculture and industrial activities have led to a huge increase in nutrient inputs to Chinese coastal waters1,2,3,4,5, which receive some the world’s highest riverine and atmospheric inputs of nutrients to the coastal ocean6,7. Nutrient inputs to Chinese coastal waters are dominated by non-point sources, largely derived from excessive fertilizer application3,8,9, while point sources, easier to control, represent less than 15% of nutrient inputs3,8. In addition, assessment of nutrient inputs to the Yellow Sea of China identified atmospheric deposition as the main vector for nutrient inputs to the coastal ocean, supplying twice the nutrient inputs delivered by rivers10. The consequences are widespread eutrophication, manifested in an increased frequency of harmful algal blooms11,12 and widespread hypoxia4,13 across Chinese coastal waters. Hence, nutrient pollution leading to coastal eutrophication is recognized as one of the most significant environmental problems, posing a great challenge to China1,3,12.
The rise of seaweed aquaculture represents a parallel major development in Chinese coastal waters14,15, with seaweed aquaculture production rising 7.7 fold from 259,839 t dry weight (DW) in 1978 to 2,004,600 t DW in 201416, growing at 7.96% year−1 at present (Fig. 1). China dominates seaweed aquaculture production worldwide, contributing over 2/3’s of global production15,17. This production is mainly comprised of Saccharina japonica and Gracilariopsis spp.18, with other species accounting for 17.3% of production16. Individual seaweed farms have reached such an extent as to be visible from space, with individual farms spanning more than 35 km2 along the coastal regions of China14 (Fig. 2).
The scale of seaweed aquaculture in China is such that it may be of regional biogeochemical significance14,15,17,19. In particular, seaweed take up dissolved nutrients, which are then removed from coastal waters to land after harvest19,20,21. Indeed, it has been hypothesized that macroalgal production helps remove excess nutrients and replenish oxygen in water, thereby alleviating the effects of eutrophication on coastal ecosystems18,19,22,23,24. Yet, the role of seaweed aquaculture as a vector for the removal of nutrients from Chinese coastal waters has not yet been evaluated. Here we demonstrate that Chinese seaweed aquaculture plays a significant role in removing nutrients from Chinese coastal waters. We do so by first providing a first order estimate of the magnitude of nutrient removal by Chinese seaweed aquaculture and then assessing its significance by comparing the magnitude of nutrient removal, per unit area and across the entire Chinese coastal zone, with that of nutrient inputs.
Results and Discussion
The magnitude of nutrient removal by Chinese seaweed aquaculture is dependent on the yield and the nutrient concentration in the seaweed tissues, which depends, in turn, on the species composition. Seaweed production reached two million t DW in 201416, growing at 7.96% year−1 at present (Fig. 1). Provided a mean (±SE) reported nitrogen (N) and phosphorus (P) concentration for the dominant species in Chinese aquaculture of 3.71 ± 1.15N % DW and 0.52 ± 0.23P % DW for Saccharina japonica, 4.53 ± 0.43N % DW and 0.34 ± 0.05P % DW for Gracilariopsis spp., and an estimated average concentration of 3.52 ± 0.40N % DW and 0.38 ± 0.14P % DW for the rest of the species (Table 1), the calculated N and P removal with seaweed aquaculture in 2014 was substantial, at 75,371 ± 18,424 t N and 9,496 ± 3,875 t P, respectively.
Seaweed aquaculture in China is characterised by a yield of about 1,604 t DW km−2 16, corresponding, using the estimated average tissue N and P concentration in seaweed aquaculture provided above, to a removal of 60.31 t N and 7.60 t P km−2 seaweed farm per year (Table 1). Nitrogen and phosphorus inputs are largely derived in inorganic form, but include a small fraction of dissolved organic nitrogen and, even small, dissolved organic phosphorus25. However, seaweed have been shown to be able to take up low-molecular forms of dissolved organic nitrogen as well26,27. The calculations of nutrient removal by seaweed aquaculture in China presented above involve no assumptions as to the form of nitrogen or phosphorus supporting the uptake. Resolving regional variability in nutrient inputs and seaweed production would require additional information that is currently unavailable. We hope that the calculations above will provide a stimulus to generate the data required for regional analysis and to examine directly the uptake by seaweed of nutrient deposited from the atmosphere.
The estimates provided above confirm the important contribution of Chinese seaweed aquaculture to nutrient removal in China. This capacity is further confirmed by reports of reductions in dissolved inorganic nutrient concentrations in Chinese seaweed farms. Published case-studies assessing nutrient removal in four seaweed farms in China indicate that the nutrient concentrations in seawater decreased by, on average (±SE), 53% ± 7%, 47% ± 10% and 47% ± 3% for NH4-N, NO3-N and PO4-P, respectively, within these seaweed farms compared to that in nearby non-cultivation coastal waters (Table 2). Total N and P removal by seaweed aquaculture represents 5.56% and 39.60% of the total estimated input of N and P to Chinese coastal waters of 1,350,053 t N and 23,982 t P, respectively, with the N removed with seaweed aquaculture representing about 66% of the total point source inputs to Chinese coastal waters3,8. This nutrient removal capacity is remarkable, provided that seaweed aquaculture occupies only about 1,250 km2 of coastal area. This represents only approximately 0.3% of the area of Chinese territorial sea waters28, suggesting that there is ample scope to continue to increase the seaweed aquaculture area further. Indeed, we calculate that one km2 of seaweed farm removes the annual N and P inputs received by 17.8 km2 and 126.7 km2 of Chinese coastal waters, respectively (Table 1), providing an estimate of the nutrient removal footprint area of Chinese seaweed farms.
The seaweed area required to remove N and P equivalent to the 100% of the present N and P inputs to Chinese coastal waters can be calculated, as the ratio of the total input estimate provided above and the removal rate by seaweed farms per km2, at 22,470 km2 for N and 3,155 km2 for P, respectively. Whereas removal of the total N inputs to Chinese coastal waters requires a seaweed farming area 17 times larger than the extant area, one and a half times more of the seaweed area would be able to remove close to 100% of the P inputs. At the current annual rate of 7.96% increase in seaweed aquaculture16, the area required to remove 100% of the P inputs will be met by 2026. Although fast urbanization in China may still enhance inputs of nutrients to coastal area in the following decades1,29, causing further increase of total riverine N and P inputs by 30–200% to 205029, the rapidly developing seaweed aquaculture would have the capacity to remove almost all the riverine inputs of P and much of N inputs. Hence, the efficiency of seaweed farming in removing nutrients from coastal waters may lead to phosphorus limitation in the future, even under the large nutrient inputs to Chinese coastal waters, thereby preventing the proliferation of dense algal blooms. These are, however, theoretical calculations, as neither nutrient inputs nor seaweed farms are, or will be, homogeneously distributed along the coast. Moreover, phytoplankton and wild and aquaculture seaweed will compete for nutrient inputs, particularly as further growth of seaweed aquaculture results in reduced nutrient concentrations in Chinese coastal waters. The much larger biomass density (g DW m−3) in seaweed farms compared to phytoplankton and the fact that seaweed biomass is typically near the surface in aquaculture farms suggest that seaweed might be able to take up the bulk of the atmospheric nutrient deposition in farmed areas, an important component of the nitrogen input to Chinese coastal waters.
Nutrient concentrations are expected to decline with increasing expansion of seaweed farming, to the extent that seaweed aquaculture may in the future become nutrient limited, particularly in areas supporting large seaweed farms and moderate or low nutrient inputs. Seaweed aquaculture may overcome future nutrient limitation by integrating it with animal aquaculture in polyculture, thereby using the nutrient emissions from animal metabolism and excess feed to maximize economic, environmental and ecological benefits18. Nevertheless, the annual growth rate of 7.96% can only be sustained if farming continues to be economically profitable in China, which requires a parallel rise in the domestic and worldwide demands for seaweed products. This requires an increase in per capita seaweed consumption, diversification of outputs to other industries, as well as economic compensation, possibly as tax relief or direct subsidies, to seaweed farmers for the benefits of the activity in terms of nutrient removal.
In conclusion, we demonstrate here that seaweed aquaculture has reached a scale in China where it is already delivering considerable environmental benefits in terms of nutrient removal from coastal waters. Further growth of seaweed aquaculture can play a pivotal role, along with sustained efforts to reduce nutrient inputs, in tackling the hitherto mounting problem of coastal eutrophication in China.
We extracted aquaculture seaweed production and percentage of major seaweed cultivation from annual government fishery reports in China for 37 years30 from 1978 to 2015 (Fig. 1). Then, we obtained the current Chinese seaweed yield (t DW km−2) by dividing the 2014 production by the 2014 seaweed aquaculture area, both reported in June, 201516.
We used published estimates of tissue N and P concentration of Chinese seaweed aquaculture species based on a search on Web of Science® and CNKI® accessed until December 2015. The search using “nutrient concentration”, “China” and “seaweed” as keywords yielded a total of 22 papers reporting nutrient concentration of seaweed species in China. From these papers, we selected those corresponding to the seven main targeted species of seaweed aquaculture in China (Tables S2–1 and S2–2), and calculated their mean (±SE) nutrient concentration. We then combined the average tissue nutrient concentration with the contribution of each species to aquaculture production in China (in 2014) to yield a weighted-average nutrient concentration in seaweed aquaculture in China (Tables S2–3). We combined the weighted-average nutrient concentration with the average yield of seaweed aquaculture in China to calculate nutrient removal per km2 for Chinese coastal areas.
Estimates of nutrient inputs are not available for the entire Chinese territorial sea waters, but detailed budgets have been reported for the Yellow Sea10 and East China Sea31, including both nutrient inputs with riverine discharge and atmospheric inputs. These were used to calculate the total input of N and P to the 0.4 million km2 of Chinese territorial sea waters28 where seaweed aquaculture is based. We first calculated the flux of N and P per km2 for the Yellow Sea, which was reported as the yearly nutrient input from riverine and atmospheric sources10, by diving the total input by the area of this ecosystem. For the East China Sea, the nutrient input, including riverine discharge and atmospheric inputs, was reported for each of two seasons31. We then divided the average input by the area of this ecosystem to obtain the flux of N and P per km2. We then combined the two estimates for the Yellow Sea and East China Sea as a weighted-average flux to obtain a characteristic nutrient flux per km2 (t yr−1 km−2), to Chinese coastal waters, and multiplied this estimate by the 0.4 million km2 of Chinese territorial sea waters28 to obtain the total nutrient input to Chinese coastal waters. The estimates obtained were consistent with an independent estimates of the total nutrient input to the East China Sea32. These estimates of nutrient inputs are likely to produce an upper estimate of fluxes, and therefore a lower estimate of removal with seaweed aquaculture, as the Yellow Sea and East China Seas receive particularly high nutrient inputs10,31. All statistical analyses were conducted using JMP v10 software.
How to cite this article: Xiao, X. et al. Nutrient removal from Chinese coastal waters by large-scale seaweed aquaculture. Sci. Rep. 7, 46613; doi: 10.1038/srep46613 (2017).
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This study was supported by the International Science & Technology Cooperation Program of China (2015DFA01410) and the National Natural Science Foundation of China (21677122). Anqi Wang assisted in making Figure 2.
The authors declare no competing financial interests.
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Xiao, X., Agusti, S., Lin, F. et al. Nutrient removal from Chinese coastal waters by large-scale seaweed aquaculture. Sci Rep 7, 46613 (2017). https://doi.org/10.1038/srep46613
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