Marine fishing is the primary means of obtaining marine aquatic products (Moffitt and Cajas-Cano, 2014). Although the catch in China Seas remains high, with the continuous increase in fishing efforts, changes in the marine climate, and environmental degradation, more and more commercial fish species in China’s waters have been over–exploited, causing a decline in resources, which seriously hinders the sustainable utilization of fishery resources (Shi and Chen, 2019). As an important basis for fishery resource management, stock assessment can accurately evaluate the biological reference points such as fisheries biomass, allowable catch, and maximum sustainable yield using mathematical statistical methods based on life history patterns and the quantification of fishery resources and commercial fishing (Hilborn and Walters, 1992; Quinn and Deriso, 1999). Traditional fish stock assessment methods require many parameters. In addition to statistical data, they need more complete survey data, such as long–term reliable catch yield data, density indices of resources, age/length structure data, and even tagging and releasing data (Methot and Wetzel, 2013). Obtaining this information requires technical know–how, skilled workers and financial support, and is therefore inconvenient when evaluating data–limited fisheries–as is the case for more than 80% of the world’s stocks, with only 1% of fish species having been systematically assessed (Costello et al., 2012). Due to the belated onset of fishery resource surveys in the China sea, the paucity of recorded survey data for most fisheries makes it difficult to evaluate them with traditional fish stock assessment methods. Stock assessments based on the existing data require the application of stock assessment methods applicable to data–limited fisheries to carry out fisheries stock assessment in China’s marine areas.

The East China Sea lies to the east of the Chinese mainland and is the marginal sea of the Western Pacific Ocean. Marine capture yield in the East China Sea accounts for more than 40% of the total output of China’s ocean fishing industry (Fishery Management Bureau of Ministry of Agriculture and Rural Affair (FMBMARA), (2000–2021)).

Trichiurus lepturus, distributed in the Western Pacific and Indian Ocean, belongs to Perciformes, Trichiuridae family, and the Trichiurus genus. Three Trichiurus species, T. lepturus, Trichiurus nanhaiensis and Trichiurus brevis, are distributed in China Seas (Hou et al., 2021; Hsu et al., 2022). Among them, Trichiurus in the East China Sea is mainly T. lepturus (Hsu et al., 2022).There are two migration routes for T. lepturus, most specimens migrated southward from the Yellow Sea to the ECS and South China Sea, and some specimens migrated northward from the South China Sea to the Taiwan Strait (He, 2019; Hsu et al., 2022). It is a commercially important species in China’s fishery in the East China Sea, harvested by bottom trawl, longline fishing, bag seine, and tow net operations. The catch of T. lepturus in the East China Sea showed an upward trend from the early 1950s to 1974, after which its downward trend reached its lowest level in 1988. After the protection of breeding individuals and young fish due to the establishment of the fishing system in the summer season in 1995, the annual catch of T. lepturus increased significantly, and the catch has continued to exceed 800, 000 tons since 1998. Since 2006, because the fishing effort has exceeded the bearing capacity of the resources, the catch of T. lepturus has shown a downward trend, with catch in 2020 of less than 600, 000 tons (Zheng et al., 2013; Fishery Management Bureau of Ministry of Agriculture and Rural Affair (FMBMARA), (2000–2021)). Studies on T. lepturus in the ECS included its life history characteristics (Panhwar et al., 2018), migrations (Sun et al., 2020), population genetics (Hsu et al., 2022), and reproductive protection (Chiang et al., 2002), with the studies of its resource status obtained using mostly the Beverton–Holt model (Ling et al., 2008), yield per recruit model (Cao and Liu, 2007), and surplus production model (Wang and Liu, 2013). T. lepturus is one of the most abundant species of marine fish in China, but its CPUE data is relatively lacking, which leads to some flaws in the evaluation results obtained using traditional fishery resource evaluation models. It is therefore crucial to carry out appropriately effective, reasonable, and accurate fishery resource assessment for T. lepturus. However, in the ECS the stocks had not been assessed based on data limited methods for the species.

Body length data can be used to fit and calculate biological parameters such as growth rate, mortality, and population size, and then evaluate the resource status of its population (Petrakis and Stergiou, 1995; Stergiou and Moutopoulos, 2001). The resource assessment models based on body length data include mainly LBSPR (Hordyk et al., 2015), LIME1 (Rudd and Thorson, 2018), LBB (Froese et al., 2018) and LBRA (Ault et al., 2019) models. Among them, The LBB model, which does not need to input data other than body length frequency data, has the advantage of lower input data requirements. Based on the survey data of trawling nets, we used the LBB method to analyze length frequency data from 2016 to 2020, and calculate the population evaluation indices such as asymptotic body length, growth, and death coefficients of T. lepturus in the East China Sea, in order to provide an evidential basis for the resource assessment of T. lepturus in the East China Sea, and to promote the management of fishery resources at the level of sustainable utilization in this area.

The estimated L_inf distribution range of T. lepturus in the East China Sea over the years was 49.3-76.9 cm ( Table 3 ), which was higher than the average of 42.8 (41.7-44.8) cm ( Table 2 ) estimated in this study based on LBB from 2016 to 2020, indicating that T. lepturus in ECS comprises mainly small individuals smaller than in the past. This may be the response of of T. lepturus to continuous high–intensity fishing, which was caused mainly by the selectivity of the nets to the species during the fishing operation and the different methods used for research. On the one hand, due to high–intensity fishing activities, a large number of larger individuals will be removed (Enberg et al., 2012), which has changed the population structure of T. lepturus, and hence the proportion of small individual in the population is increasing. In the study of Trichiurus in the South China Sea, due to long–term high–intensity fishing, the L_inf decreased from 62.2 cm in the 1980s to 58.5 cm in 2014–2015 but the average anal length showed signs of recovery after the fishing pressure was eased (Shi et al., 2020). This positive effect on the biological characteristics of fish due to factors such as fisheries policy also exists for other fish species, such as Evynnis cardinalis (Zhang et al., 2020) in the Beibu Gulf of the South China Sea, and Oncorhynchus keta (Fukuwaka and Morita, 2008) in Hokkaido, Japan. The L_inf of T. lepturus varied greatly among different sea areas and there was no obvious law, which was confirmed by the results of Zhang et al. (2022) and Amador and Aggrey-Fynn (2020). On the other hand, the L_inf estimated based on LBB depends on the length distribution of the population represented by the length frequency data, which was different from the results estimated by other methods (Wang et al., 2018). If the proportion of supplementary population in the population is high, the estimated L_inf of LBB will be reduced (Froese et al., 2018). In recent years, the catch of T. lepturus in the East China Sea had a large proportion of small individuals (Zhou et al., 2002), leading to fluctuations in the estimated L_inf in different years. However, it was obvious that the L_inf of T. lepturus in this study was significantly smaller than that in other sea areas of China. Similarly, there were differences in L_inf of T. lepturus in different sea areas of India.The habitat and fishing intensity in different sea areas are also the main factors causing the difference of T. lepturus individual size (Bernatchez, 2016).

In this study, the estimates of F/M > 1 and E > 0.5 suggested that the stock was overfished, while the estimates of B/Bo < 0.5 showed that the current biomass was very low. This result was compared with other studies ( Table 4 ). Our result was confirmed by the studies published by other researchers (Ling et al., 2005; Ling et al., 2008; Wang, 2010; Wang and Liu, 2013; Zhang & Chen, 2015; Panhwar et al., 2018), where Beverton–Holt, yield per recruit, surplus production and per unit recruitment models were used to assess the resource of T. lepturus in ECS, with all results showing the stock was suffering from overfishing ( Table 4 ). Compared with the LBB model, other models have the disadvantages of low accuracy of assessment results and difficulty in obtaining the required data for data-limited fisheries. For example, the surplus yield model does not consider the biological characteristics of the research object, resulting in the lack of corresponding biological interpretation of the evaluation results, and cannot reflect the impact of environmental factors on fish population dynamics (Hilborn & Walters, 1992; Zhan, 1995). In addition, because most of the fisheries in China’s offshore waters are mixed fisheries, the catches and fishing methods are diversified, and the statistical yield data may be higher than the real value (Watson and Pauly, 2001; Xu et al., 2003), which will also lead to the evaluation results of MSY and B _MSY.

Although T. lepturus has been overfished, its resources have not decreased as sharply as those of the the large yellow croaker (Liu and Mitcheson, 2008), and its catch has remained at a high level, which may be related to three factors. First, the reproductive characteristics of T. lepturus make it possible to generate more supplementary populations under overfishing. Studies have shown that T. lepturus has a long spawning period and a wide distribution of spawning individuals, and can reach sexual maturity at only one year (Tang et al., 2006; Chen et al., 2013), which provides a certain resilience. Second, the seasonal fishing moratorium and the protection measures for T. lepturus spawning grounds implemented in the ECS provide a guarantee for the growth and reproduction of T. lepturus. A new summer fishing moratorium policy has been implemented in the ECS since 1995. The fishing moratorium from May to June stipulated by the policy coincides with the peak spawning period of T. lepturus (Zhang et al., 2017b), and many types of fishing are not allowed to operate during this period, which allows for substantial increases in the supplementation of T. lepturus. Third, there may be hidden increased effort due to electronics and increasing experience of fishers. Fishing boats in the ECS have greater power and are equipped with more advanced technology than before. Such effort creep will capture an increased proportion of the population, thereby keeping catches stable while the stock is declining.

The novel aspect of this study is that few studies have applied data–limited method based on length frequency data to the resource assessment of T. lepturus in the East China Sea. In this study, B/B ₀ and L_c were lower than B_MSY /B ₀ and L_{c_opt} , respectively, indicating that the catch should be reduced and fishing should start at larger size. Faced with the situation of overfishing of T. lepturus in the ECS, we should first reduce the fishing intensity and the catch of T. lepturus. However, the decline in fishing horsepower was low despite the significant decrease in the number of fishing vessels, indicating that the fishing pressure on fishery resources remained high ( Figure 4 ). The large number of fishermen in the ECS and other factors mean that fishing efforts cannot quickly be reduced to a reasonable level, so that the effect of the recent measures to reduce the fishing horsepower is not obvious. Second, protecting juvenile fishes can effectively improve the resource level of T. lepturus in the ECS. The mesh size of fishing gear used by fishing vessels–especially the two–stick swingnet–is too small (3.5 cm, the minimum mesh size of two–stick swingnet should be 8.8 cm (Zhuang et al., 2022), which prevents young fish in the catch from being released; they are consequently caught in large quantities and the population structure tends to be miniaturized and younger, which limits the spawning stock biomass per recruit (Zhang et al., 2017a). While continuing to implement the fishing moratorium policy, by increasing the mesh size of the nets, it is also possible to increase the escape rate of juveniles; strict adherence to the catchable specifications will also reduce the capture of juveniles, thus achieving the conservation of juveniles in the ECS.

The original contributions presented in the study are included in the article/supplementary material. Further inquiries can be directed to the corresponding authors.

Ethical review and approval was not required for the animal study because the samples we studied were all from frozen fishes caught in commercial fishing activities.

KZ: Conception and design of this study, Acquisition of data, Visualization, Software, Writing–original draft. WZ: Writing–review & editing. YS: Writing–review & editing. All authors contributed to the article and approved the submitted version.