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Article

Population Genetics of the Endemic Hemiculterella wui (Wang, 1935) in the Poyang Lake Basin (China)

by
Qin Ma
1,2,†,
Mingzheng Li
1,† and
Huanzhang Liu
1,*
1
The Key Laboratory of Aquatic Biodiversity and Conservation, Institute of Hydrobiology, Chinese Academy of Sciences, Wuhan 430072, China
2
School of Life Sciences, Nanchang Normal University, Nanchang 330032, China
*
Author to whom correspondence should be addressed.
†
These authors contributed equally to this work.
Fishes 2024, 9(7), 260; https://doi.org/10.3390/fishes9070260
Submission received: 14 May 2024 / Revised: 26 June 2024 / Accepted: 2 July 2024 / Published: 3 July 2024
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Abstract

:
The Yangtze River floodplain is an area with an extremely rich diversity of fish species. Poyang Lake, as an important part of this river–floodplain system, is a crucial habitat for the survival of fish. However, prolonged human activities, such as environmental pollution and hydroelectric development, have degraded the habitat in the Poyang Lake Basin, posing threats to fish populations. Understanding genetic diversity is crucial for maintaining fish populations and understanding their dynamics. The genetic diversity of Hemiculterella wui, an economically endemic species in China of subfamily Cultrinae (Cypriniformes: Cyprinidae), has been understudied. This study investigated the genetic diversity and structure of H. wui populations from the Ganjiang, Xinjiang, Fuhe, and Raohe rivers in the Poyang Lake Basin using mitochondrial Cytb gene analysis. Results showed high haplotype diversity but low nucleotide diversity in H. wui’s Cytb sequences. Analysis of molecular variance (AMOVA) showed no significant geographic genetic structure among populations. Haplotype network analysis revealed no clear geographical clustering. Neutrality tests and haplotype nucleotide mismatch distribution indicated that all populations had experienced expansion events. These findings suggest that H. wui in Poyang Lake does not show a distinct geographic structure. However, it is still necessary to monitor the genetic characteristics of H. wui to maintain the genetic diversity of fishes in Poyang Basin, considering the threat of habitat loss and fragmentation to the population.
Keywords:
Hemiculterella wui; genetic diversity; population genetic structure; riverine fish
Key Contribution: This work reveals the genetic diversity and structure of different geographical populations of H. wui in the Poyang Lake Basin and provides a scientific foundation for the conservation and utilization of its resources.

1. Introduction

Poyang Lake is the largest freshwater lake in China, being a typical seasonal shallow lake. It is located at the junction of the southern bank of the middle and lower reaches of the Yangtze River. The watershed area of Poyang Lake is 162,200 km2, accounting for 9% of the Yangtze River drainage area. It recharges freshwater from five tributary rivers, the Ganjiang River, the Fuhe River, the Xinjiang River, the Raohe River, and the Xiushui River. The five rivers converge in Poyang Lake and then discharge to the Yangtze River at Hukou, a county in Jiangxi Province, forming a complete radiating water system with Poyang Lake as the convergence center [1,2]. In the flood season, the inflow from the Yangtze River and the five other rivers exceeds the outflow of Poyang Lake. In contrast, in the dry season, the inflow from the Yangtze River and the five tributary rivers is less than the outflow from Poyang Lake. Due to the combined effects of hydraulic interactions between the Yangtze River and Poyang Lake and the Poyang Lake catchment inflow, the Yangtze River–Poyang Lake River–Floodplain ecosystem is formed. This unique ecosystem, shared with Dongting Lake, supports a rich diversity of aquatic flora and fauna, leading to abundant fish species. The Poyang Lake Basin alone records 236 different fish species [3].
Hemiculterella wui (Wang, 1935) is a small-sized economic species of the subfamily Cultrinae (Cypriniformes: Cyprinidae). Hemiculterella is a genus with three endemic species in China, namely, H. Sauvagei Warpachowsky, 1887; H. Macrolepis Chen, 1989; and H. wui. Hemiculterella sauvagei, which is endemic to the upper reaches of the Yangtze River, having been well studied. Hemiculterella macrolepis is distributed in the tributaries of the Lancang River in China and primarily inhabited in mountain streams, lacking research. Compared to the previous two species, H. wui has a relatively more extensive distribution, predominantly found in the Pearl River system and the Qiantang River system [4,5,6,7,8]. However, recent surveys have discovered the presence of H. wui in the Poyang Lake Basin.
Initial documentation of H. wui in the Poyang Lake Basin dates back to 1996 by Zhang et al. [6], who studied the fish fauna in northeastern Jiangxi Province, including the Xinjiang River and the Raohe River. They noted the presence of H. wui, although specific collection sites were not detailed. Subsequent surveys from 2014 to 2018 by Liu et al. [7] in 11 rivers of the Luoxiao Mountains, including Xiushui River and tributaries of the Ganjiang River (including the Suichuan River and the Shangyou River), also recorded the presence of H. wui. Additionally, Wang and Zhang [8] surveyed the Ganjiang River system between 2016 and 2017, gathering specimens of H. wui. These findings suggest that H. wui may have a relatively extensive distribution in the Poyang Lake Basin, though further research is necessary for confirmation.
In recent years, due to the impact of global climate change and human activities, such as dam construction, the ecological protection of Poyang Lake has faced severe challenges. In river ecosystems, dam construction is one of the main factors leading to river fragmentation, potentially reducing the reproductive success of fish species inhabiting the river [9,10]. Then, it will lead to a decline in fish resources. Dams will affect the normal movement of fish species throughout a river system [11,12]. They may lead to population isolation, decreased gene exchange, and increased genetic drift, which in turn affects the ability of populations to cope with environmental changes and threatens global freshwater biodiversity [13,14,15]. Most studies suggest that habitat fragmentation will negatively impact the genetic diversity and genetic structure of fish populations [16,17,18,19]. However, it has also been shown that dam-induced habitat fragmentation does not reduce the genetic diversity of fish populations in a short period, nor does it cause population differentiation [20,21]. Therefore, the genetic diversity of the fish population can not only help to understand the genetic status of fish but also can be used to analyze the impact of dam construction on fish genetic diversity to provide targeted strategies for fish resource conservation. This highlights the need for a better understanding of the genetic resource status of H. wui. Despite its ecological and economic importance, research on H. wui remains limited. It has been mentioned in various fishery resource surveys [6,7,8,22,23], early resource investigations [24], studies related to its length–weight relationship [25,26], DNA barcoding research [27], and the mitochondrial genome of H. wui [28]. However, there is a lack of information regarding the genetic diversity of H. wui.
In this study, we conducted an extensive fish resources survey of H. wui in the Poyang Lake Basin, including the Ganjiang River, Xinjiang River, Changjiang River, and Fuhe River. Utilizing the mitochondrial cytochrome b (Cytb) gene, the study explores the genetic diversity and structure of different geographical populations of H. wui in the Poyang Lake Basin. The objective is to gain insights into genetic diversity and structure of this species, thereby providing a scientific foundation for the conservation and utilization of its resources.

2. Materials and Methods

2.1. Study Area

Poyang Lake, located in Jiangxi Province, has five tributaries: the Ganjiang River, the Fuhe River, the Xinjiang River, the Raohe River, and the Xiushui River. The Ganjiang River, the largest tributary of Poyang Lake, is located to the southwest of the Poyang Lake and has seven large dams. The Fuhe River, the second largest tributary of Poyang Lake, is located to the southeast of Poyang Lake, and it features two large dams. The Xinjiang River and the Raohe River are located to the east of Poyang Lake. There are three large dams in the Xinjiang River. The Raohe River divides into two branches: the northern branch is called the Changjiang River, and the southern branch is called the Le’an River. The Le’an River is longer than the Changjiang River, so it is generally used as real sources of the Raohe River. The southern and northern branches converge in Yaogongdu, Poyang County. Four dams have been built in the Changjiang River, whereas no dams have been constructed in the Le’an River. The remainder is the Xiushui River, the only tributary of Poyang Lake that was not studied in this study.

2.2. Sample Collection

During July and August 2020, comprehensive fishery resource surveys were carried out in multiple Poyang Lake water system locations. We set up sampling sites in different sections of four tributaries in the Poyang Lake Basin to understand whether there were differences in genetic diversity among different geographic populations, as well as to explore whether dams affected the genetic diversity of populations. These included two sections of the Ganjiang River in Wan’an county and Xiajiang county in Ji’an city, two sections of the Xinjiang River in Guangfeng district of Shangrao City and Yuehu district of Yingtan City, two sections of the Raohe River in Changjiang district of Jingdezhen City and Fuliang county in Jingdezhen City, and a section of the Fuhe River in Fuzhou City. A total of 231 samples of H. wui were collected using gillnet from areas from the seven above-mentioned sites. Detailed information about the sampling locations and their corresponding water systems is provided in Table 1 and illustrated in Figure 1. For each fish, the right dorsal muscle was collected and preserved in 95% ethanol, and then it was subsequently transported to the laboratory for further analysis.

2.3. DNA Extraction and PCR Amplification

DNA was extracted from the animal tissue samples using the OMEGA animal tissue DNA extraction kit (OMEGA, Beijing, China), adhering to the kit’s specified protocol. Post-extraction, the DNA concentration was ascertained using 1.0% agarose gel electrophoresis and a UV spectrophotometer. The mitochondrial Cytb gene was then amplified using primers L14724 (5′-GACTTGAAAAACCACCGTTG-3��) and H15915 (5′-CTCCGATCTCCGGATTACAAGAC-3′) [29].
The PCR reaction mixture, totaling 30 µL, comprised 3.0 µL of 10× PCR buffer (with Mg2+), 1.5 µL of dNTPs (2.5 µmol/µL), 0.75 µL each of forward and reverse primers (10 pmol/µL), 0.15 µL of EasyTaq DNA polymerase (5 U/µL, TransGen Biotech, Beijing, China), 3 µL of template DNA (0.05 g/L), and the remainder filled with sterile double-distilled water.
The PCR amplification was conducted on a Thermal cycler (Bio-rad, Singapore), under the following procedure: initial denaturation at 94 °C for 5 min, followed by 35 cycles each of denaturation at 94 °C for 30 s, annealing at 56 °C for 1 min, and extension at 72 °C for 1 min. This was concluded with a final extension at 72 °C for 10 min.
After PCR, the amplified products were detected by 1.0% agarose gel electrophoresis. The PCR products with clear and bright target bands (almost 1200 bp) were sent to Wuhan Tianyi Huayu Gene Technology Co., Ltd. for purification and sequencing. For data reliability, bidirectional sequencing was performed using primers L14724 and H15915.

2.4. Data Analysis

The obtained bidirectional sequences were checked by comparing them with the sequence peak plots. The sequences were assembled in both directions based on the contigs using the SeqMan Ultra analysis program from the DNAStar Lasergene software (version 17.2.1, DNASTAR, Inc., Madison, WI, USA). The alignment and trimming of the assembled sequence were conducted using MEGA 7.0 [30] software, with sequencing peak graphs cross-referenced to identify and correct potential sequence errors. Analysis of nucleotide composition and variations was also performed. The transition/transversion ratios were calculated based on the Kimura two-parameter model [31]. The same model was used to calculate pairwise distances between individuals, which is used to identify whether two individuals are of the same species. The criterion is that the genetic distance between sequences of two individuals of the same species is less than 2% [32]. DnaSP 5.0 software [33] was utilized to calculate the number of haplotypes (N), polymorphic sites, haplotype diversity (Hd), nucleotide diversity (Pi), variable sites, singleton sites, and parsimony-informative sites.
DnaSP 5.0 was used to generate an arp file, which was imported to Arlequin v 3.1 [34] to calculate haplotype frequencies in populations. Then, the haplotype data and haplotype frequencies in populations were merged to form a Nexus file in Notepad++. The Nexus file was used to draw the Haplotype network diagram using POPART 1.7 [35], employing the Median-joining method to examine evolutionary relationships among different haplotypes.
Arlequin v 3.1 software was used for the hierarchical analysis of molecular variance (AMOVA), with 10,000 permutations implemented. According to the river source, the seven populations were divided into four groups: the Xiajiang and Wan’an populations formed one group, the Yujiang and Guangfeng populations formed another, the Changjiang and Fuliang populations were grouped together, and the Fuzhou population formed a group. Population genetic differentiation coefficients (F-statistics, FST) were calculated with 10,000 permutations by Arlequin 3.1. The same software was used for neutral tests, including Tajima’s D, Fu’s Fs, and nucleotide mismatch analysis, to deduce the population history demography (e.g., bottlenecks or expansions).
Population expansion time (T) was estimated in Arlequin v 3.1 using the formulas τ = 2 ut and T = tC, where τ is Tau, a moment estimator, which represents a unit of mutational time; t represents the number of generations experienced since the expansion; and C is the number of generations. The substitution rate per site was calculated using the formula u = µk, where k is the sequence length, and µ is the sequence’s evolutionary rate. µ was assumed to be 0.76% per million years (MY), the mutation rate in cytochrome b of Cyprinid [36].

3. Results

3.1. Sequence Features and Population Genetic Diversity

The alignment and correction of the mitochondrial Cytb sequence of H. wui yielded a consistent sequence length of 1141 base pairs across all samples. Notably, these sequences showed neither insertions nor deletions. The number of transitions exceeded that of transversions, with an average transition/transversion ratio (Ti/Tv) of 6.28. The genetic distance between pairs of the 231 Cytb gene sequences ranged from 0.000 to 0.009, less than 0.02 [32], indicating relatively low genetic variation. The sequences exhibited 71 nucleotide variation sites, constituting 6.22% of the total sequence length. This included 39 singleton variable sites and 32 parsimony informative sites.
The base composition analysis revealed the average contents of A, T, C, and G bases as 27.9%, 26.2%, 30.0%, and 15.9%, respectively. The A+T content (54. 1%) was significantly higher than C+G content (45.9%), indicating a strong AT bias and an anti-G bias, a characteristic common to mitochondrial DNA genes in other vertebrates [37].
In total, 65 different haplotypes were identified in the Cytb gene sequences of H. wui (GenBank with the accession numbers of PP645203-PP645267). The overall sample displayed a haplotype diversity (Hd) of 0.914 ±0.014 and a nucleotide diversity (Pi) of 0.0023 ±0.0001. Among the seven populations studied, the Xiajiang population exhibited the highest haplotype diversity (0.948 ± 0.018), but the Changjiang population revealed the lowest haplotype diversity (0.802 ± 0.069) (Table 1). The Guangfeng population had the highest nucleotide diversity (0.0028 ± 0.0004), and the Changjiang population had the lowest nucleotide diversity (0.0012 ± 0.0003).

3.2. Population Genetic Differentiation

The analysis of molecular variance (AMOVA) revealed that a considerable majority (97.6%, FST = 0.02400, p < 0.01) of the genetic variation was within these populations. In comparison, 1.57% (FCT = 0.01575, p > 0.05) was due to variation between groups, and a mere 0.83% (FSC = 0.00839, p < 0.05) resulted from variation among populations within groups (Table 2).
Pairwise FST values showed negligible differences (p > 0.05), except in a few cases (YJ and XJ, CJ and XJ, FZ and WA, YJ and WA, CJ and WA, FL and WA, and GF and FZ). The FST values ranged from –0.0018 to 0.0481 (Table 3).

3.3. Haplotype Network

From the 231 H. wui samples analyzed, 65 haplotypes were identified through the Cytb gene sequence. There were 17 common haplotypes detected among the populations, with Hap_3 being distributed in all populations with relatively high frequency, suggesting it might be an ancient haplotype. The other haplotypes appeared to have evolved directly or indirectly from it. These haplotypes were dispersed across different geographic populations without forming a distinct systematic geographical distribution pattern (Figure 2).

3.4. Historical Demography Analysis

Tajima’s D and Fu’s Fs are two commonly used indicators for inferring population history. Tajima’s D value being higher than zero suggests the population might have experienced a bottleneck effect or balancing selection. If Tajima’s D value is notably less than zero, the population might have experienced population expansion and directional selection [38]. Fu’s Fs neutral test, rooted in coalescent theory, indicates population expansion through values significantly less than zero [39]. In this study, both Tajima’s D and Fu’s Fs tests yielded negative values for the overall H. wui population and its various geographic populations, achieving statistical significance (p < 0.05), as detailed in Table 4. When population has been expanded, the shape of the mismatch distribution is usually approximately unimodal, and in contrast, it shows a multimodal distribution [40,41]. The haplotype mismatch distribution analysis, depicted in Figure 3, showed unimodal distributions for both the entire population and its various geographic groups. These findings collectively suggest that the H. wui populations have undergone expansion historically. Calculations based on a mutation rate of 0.76% per MY [36] revealed the H. wui populations expanded ≈0.04–0.25 million years ago (MYA).

4. Discussion

Genetic diversity is a crucial element of biodiversity, serving as the basis and substance for populations to adapt to environmental changes. It plays a key role in preserving the adaptability and evolutionary capacity of species. Haplotype diversity (Hd) and nucleotide diversity (Pi) are essential metrics used to assess a species’ population genetic diversity. These indicators suggest that higher values correlate with greater genetic diversity within the population [42].
Similar to H. sauvagei [43], the overall population of H. wui reveals high haplotype diversity (Hd =0.914 ± 0.014). This aligns with the characteristic of small-sized fish’s populations, which often exhibit high numbers and wide distribution, thus contributing to their rich genetic diversity. However, the nucleotide diversity in H. wui (Pi = 0.0023) is lower than that of H. sauvagei (Pi = 0.0049 ±0.0070, see in [43]). Such a pattern of high haplotype diversity (Hd > 0.5) combined with low nucleotide diversity (Pi < 0.005) in H. wui could be indicative of rapid population expansion, as nucleotide diversity accumulates over a longer duration than haplotype diversity. This pattern might also suggest a relatively short evolutionary history for populations of H. wui [44,45].
The genetic structure variation of a population crucially influences its environmental adaptability [46,47]. Genetic differentiation is an essential metric for assessing a species’ genetic structure. The population genetic differentiation index (FST) commonly quantifies gene flow and genetic drift between populations. Wright [48] proposed that FST values between 0 and 0.05 indicate negligible genetic differentiation between populations; values between 0.05 and 0.15 suggest moderate differentiation; values between 0.15 and 0.25 denote severe differentiation; and values above 0.25 signify considerable differentiation. In this study, low FST values were observed within and among the populations of the four rivers for H. wui, implying that genetic interchange may exist among these populations. For example, there is low genetic differentiation between the Xiajiang and Wan’an populations in the Ganjiang River. The measures of genetic diversity were similar between the Xiajiang and Wan’an populations. The same was true for the populations above and below the dam in the Changjiang River and the Xinjiang River (Table 1 and Table 3). Contrastingly, many research projects carried out to study the effects of dams on genetic metrics have suggested that dam-induced habitat fragmentation leads to a decrease in genetic diversity and an increase in genetic differentiation in dam-isolated fish populations [19,49,50,51]. The contrary results of our study and other studies regarding the effects of dams on genetic metrics may be explained by three main factors: migration rate, generation time (G), and effective population size [52]. In this study, the earliest dam, the Wan’an Hydropower Station, was built in 1993. It corresponds to about 31 generations for H. wui (G = 1 year). At such time scales, it would likely be difficult to monitor genetic differentiation [53,54], as the accumulation of genetic variation takes a long time. The evolutionary history of populations significantly impacts genetic polymorphism patterns. The mismatch analysis and the neutral test (i.e., Tajima’s D and Fu’s Fs) proved that these populations may have experienced recent population expansions.
These expansions in the seven H. wui populations in the Poyang Lake water system are estimated to have occurred ≈0.04–0.25 MYA, mainly during the interglacial periods, particularly between the Lushan (≈0.02–0.23 MYA) and Dali glaciations (≈0.01–0.11 MYA). Interglacial periods, being warmer and more stable than glaciations, facilitate species survival and expansion from glacial refuges. Similar expansion patterns were observed in other species within the Poyang Lake basin, like Gobiobotia meridionalis Chen et Tsao, 1982 [55] and Coilia brachygnathus Kreyenberg et Pappenheim, 1908 [56].
The extensive human intervention and environmental degradation have gravely impacted the native fish populations in Poyang Lake. The current study reveals no distinct geographic structure among the H. wui populations in the four tributaries (Ganjiang River, Fuhe River, Xinjiang River, and Xiushui River) of the Poyang Lake Basin. This result suggests that the barrier may not have significantly affected genetic integrity, but the problem cannot be ignored with the increase of barrier time. Therefore, it is suggested to strengthen the monitoring and protection of the genetic diversity of the H. wui populations in the Poyang Lake Basin.
The implementation of the ten-year fishing ban in the Yangtze River Basin has led to a decrease in fishing pressure on all fish species, including H. wui, in the Poyang Lake Basin. Despite this positive management measure, the existing, under-construction, and planned water facilities in the Wu River Basin continue to pose a threat. These infrastructures will likely further disrupt fish habitats, causing significant compression or fragmentation. Such habitat alterations could impede genetic exchange among fish populations, including those of H. wui.
Understanding the population genetic diversity and structure of H. wui is crucial for developing effective conservation strategies and fishery management methods for this species and the other endemic fish with ecological habits similar to that of H. wui in the Poyang Lake Basin [57]. To formulate comprehensive protection measures, there is an urgent need to employ additional molecular markers, such as short sequence repeats (SSRs) and single-nucleotide polymorphisms (SNPs), in future research. These approaches would enable a more systematic evaluation in the genetic diversity of H. wui.

5. Conclusions

The genetic diversity of H. wui in the Poyang Lake Basin shows high haplotype diversity and low nucleotide diversity. And there is mainly low genetic differentiation within and among the populations of the four rivers (the Ganjiang River, the Fuhe River, the Xinjiang River, and the Raohe River) for H. wui. However, many dams existing in the four rivers induce habitat fragmentation, which may cause a decrease in genetic diversity and genetic differentiation among populations for a long time. Therefore, it is suggested to strengthen the monitoring and protection of the genetic diversity of the H. wui populations in the Poyang Lake Basin.

Author Contributions

Conceptualization, Q.M., M.L. and H.L.; formal analysis, Q.M.; investigation, M.L.; writing—original draft preparation, Q.M. and M.L.; writing—review and editing, H.L. All authors have read and agreed to the published version of the manuscript.

Funding

This research was funded by Scientific Research Project of Jiangxi Provincial Education Department (GJJ2202022).

Institutional Review Board Statement

The animal study protocol was approved by the Institutional Animal Care and Use Committee of the Institute of Hydrobiology, Chinese Academy of Sciences (Approval Code IHB/LL/2022028).

Informed Consent Statement

Not applicable.

Data Availability Statement

The datasets involved in this study have been deposited in GenBank (https://www.ncbi.nlm.nih.gov/genbank/) under the accession numbers PP645203–PP645267. They would be accessed on 31 May 2024.

Conflicts of Interest

The authors declare no conflicts of interest.

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Fishes 09 00260 g001
Figure 1. Sampling sites of H. wui in the Poyang Lake Basin.
Figure 1. Sampling sites of H. wui in the Poyang Lake Basin.
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Fishes 09 00260 g002
Figure 2. Haplotype network diagram of H. wui based on the Cytb gene using the POPART 1.7.
Figure 2. Haplotype network diagram of H. wui based on the Cytb gene using the POPART 1.7.
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Fishes 09 00260 g003
Figure 3. Nucleotide mismatch distribution of H. wui built using Arlequin v 3.1.
Figure 3. Nucleotide mismatch distribution of H. wui built using Arlequin v 3.1.
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Table 1. The information on sample locations and genetic diversity of H. wui in the Poyang Lake Basin.
Table 1. The information on sample locations and genetic diversity of H. wui in the Poyang Lake Basin.
RiverLocationsNumber of IndividualsNumber of Haplotypes (N)Haplotype Diversity (Hd)Nucleotide Diversity (Pi)
GanjiangXiajiang (XJ)42230.948 ± 0.0180.0027 ± 0.0003
Wan’an (WA)38190.932 ± 0.0230.0023 ± 0.0003
FuheFuzhou (FZ)33170.936 ± 0.0230.0024 ± 0.0003
XinjiangGuangfeng (GF)25130.860 ± 0.0600.0028 ± 0.0004
Yujiang (YJ)39190.916 ± 0.0310.0019 ± 0.0002
RaoheChangjiang (CJ)28100.802 ± 0.0690.0012 ± 0.0003
Fuliang (FL)26140.852 ± 0.0660.0024 ± 0.0005
Total231650.914 ± 0.0140.0023 ± 0.0001
Table 2. AMOVA analysis for H. wui among different populations on the basis of the Cytb gene. **: p < 0.01, *: p < 0.05.
Table 2. AMOVA analysis for H. wui among different populations on the basis of the Cytb gene. **: p < 0.01, *: p < 0.05.
Source of VariationdfSum of SquaresVariance ComponentsPercentage of VariationFixation Indices
Among groups38.4680.02081.57FCT: 0.01575
Among populations within groups34.9390.01090.83FSC: 0.00839 *
Within populations224289.3631.291897.60FST: 0.02400 **
Total230302.7711.3236
Table 3. FST values based on pairwise difference (below diagonal) and p-values (above diagonal) from haplotype frequencies of H. wui based on the Cytb gene.
Table 3. FST values based on pairwise difference (below diagonal) and p-values (above diagonal) from haplotype frequencies of H. wui based on the Cytb gene.
PopulationXJWAFZGFYJCJFL
XJ 0.74780.1351 0.17120.00000.00900.0631
WA−0.0074 0.03600.22520.00000.00000.0270
FZ0.01080.0224 * 0.0000 0.07210.07210.0991
GF0.00990.00800.0337 ** 0.08110.07210.0631
YJ0.0325 **0.0481 **0.01730.0252 0.09910.5045
CJ0.0401 **0.0363 **0.02310.03400.0165 0.0901
FL0.02640.0363 *0.01750.0184−0.00180.0209
*: p < 0.05; **: p < 0.01.
Table 4. Statistical test for neutrality and mismatch analysis.
Table 4. Statistical test for neutrality and mismatch analysis.
PopulationTajima’s DTajima’s D p-ValueFu’s FsFu’s Fs p-ValueTauT (MYA)
XJ−1.93860.0100−16.13280.00003.3280.19
WA−1.70000.0220−12.42380.00001.7700.10
FZ−1.71020.0210−9.77600.00002.8770.17
GF−1.42180.0660−4.78320.01204.2620.25
YJ−1.93250.0140−14.09570.00002.2890.13
CJ−1.79190.0150−5.12120.00201.3750.08
FL−2.00280.0110−7.04730.00100.6290.04
Total−2.33730.0000−26.48150.00002.7580.16
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Ma, Q.; Li, M.; Liu, H. Population Genetics of the Endemic Hemiculterella wui (Wang, 1935) in the Poyang Lake Basin (China). Fishes 2024, 9, 260. https://doi.org/10.3390/fishes9070260

AMA Style

Ma Q, Li M, Liu H. Population Genetics of the Endemic Hemiculterella wui (Wang, 1935) in the Poyang Lake Basin (China). Fishes. 2024; 9(7):260. https://doi.org/10.3390/fishes9070260

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Ma, Qin, Mingzheng Li, and Huanzhang Liu. 2024. "Population Genetics of the Endemic Hemiculterella wui (Wang, 1935) in the Poyang Lake Basin (China)" Fishes 9, no. 7: 260. https://doi.org/10.3390/fishes9070260

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