• <tr id="yyy80"></tr>
  • <sup id="yyy80"></sup>
  • <tfoot id="yyy80"><noscript id="yyy80"></noscript></tfoot>
  • 99热精品在线国产_美女午夜性视频免费_国产精品国产高清国产av_av欧美777_自拍偷自拍亚洲精品老妇_亚洲熟女精品中文字幕_www日本黄色视频网_国产精品野战在线观看 ?

    Influences of local habitat,tributary position,and dam characteristics on fish assemblages within impoundments of low-head dams in the tributaries of the Qingyi River, China

    2016-08-13 06:32:47XianLIYuRuLILingCHURenZHULiZhuWANGYunZhiYAN
    Zoological Research 2016年2期

    Xian LI, Yu-Ru LI, Ling CHU, Ren ZHU, Li-Zhu WANG, Yun-Zhi YAN,*

    ?

    Influences of local habitat,tributary position,and dam characteristics on fish assemblages within impoundments of low-head dams in the tributaries of the Qingyi River, China

    Xian LI1, Yu-Ru LI1, Ling CHU1, Ren ZHU1, Li-Zhu WANG2, Yun-Zhi YAN1,*

    1Provincial Key Laboratory of Biotic Environment and Ecological Safety in Anhui; College of Life Sciences, Anhui Normal University, Wuhu 241000, China
    2Institute for Fisheries Research, Michigan Department of Natural Resources and University of Michigan, MI 48109, USA

    ABSTRACT

    Low-head dam impoundments modify local habitat and alter fish assemblages; however, to our knowledge, the pattern of how fish assemblages in the impoundments relate to local habitat, tributary position, and dam characteristics is still unclear. We used data collected in 62 impoundments created by low-head dams in headwater streams of the Qingyi River, China, to examine relationships between fish assemblages and local habitat, tributary position,and dam characteristics. We also assessed the relative importance of the three groups of factors in determining fish species richness and composition. Linear regression models showed that fish species richness was related to substrate heterogeneity,confluence link, and dam number upstream. Redundancy analysis showed that fish species compositions were influenced by substrate heterogeneity, confluence link, dam height, dam numbers upstream and downstream. Overall, dam characteristics were more important in affecting fish species richness but less important in determining fish species composition than local habitat (i.e., substrate heterogeneity) and tributary position. Our results suggest that low-head dam may affect fish species richness in impoundments by modifying local habitat and constraining fish movement, and the relative abundances of those fish species may depend more on species habitat presences and stream size than on impoundment size and number.

    Substrate coarseness and heterogeneity;Confluence link; Dam number and area

    INTRODUCTION

    Distribution and abundance of stream fishes are influenced jointly by historical processes, abiotic and biotic factors and ecological processes (Dauwalter et al., 2008; Gilliam et al.,1993; Hoeinghaus et al., 2007).1At local scale, because of interspecific differences in physiology, behavior, and habitat preference (Jackson et al., 2001), local fish assemblages relate to stream segment habitat features, including flow regime (Yan et al., 2011), water temperature (Wang et al., 2003), dissolved oxygen (Ostrand & Wilde, 2001), and substrate size (Wang et al., 2013). Also, some stream size descriptors, such as water depth (Harvey & Stewart, 1991), stream width (Yan et al., 2010),and discharge (Chu et al., 2015a) are important factors in determining local fish diversity. At a river network scale, the nature of the continuities between mainstems and tributaries,and among tributaries, may result in spatial auto-correlation of abiotic and biotic factors and ecological processes within a watershed (Grant et al., 2007). Local fish assemblages are also determined by the tributary position within the drainage network,which determines fish immigration and extinction rates (Grenouillet et al., 2004; Taylor & Warren, 2001; Yan et al., 2011). Some descriptors of tributary position, such as link magnitude,downstream link, and confluence link, also have been reported to influence local species richness and compositions of stream fishes (Grenouillet et al., 2004; Li et al., 2014; Osborne & Wiley,1992; Smith & Kraft, 2005; Yan et al., 2011). In addition, such spatial pattern of fish assemblages and their relationship with natural environmental factors are modified by anthropogenicactivities in the stream channel or in their watersheds, such as land use, dam construction and water pollution (Chu et al., 2015a;Harding et al., 1998; Vila-Gispert et al., 2002).

    Dams are widely recognized as one of the primary means by which humans alter or modify fluvial ecosystems (Poff & Hart,2002; Rosenberg et al., 1997). Numerous investigations have revealed that dams affect stream fish in diverse ways, including blocking fish passage, altering flow and thermal regimes,modifying local habitat condition, and altering the prey base (e.g., Murchie et al., 2008; Nilsson et al., 2005; Poff & Zimmerman, 2010; Rosenberg et al., 2000; Wang et al., 2011). However, most of our knowledge on how dams affect lotic systems and fish assemblages is derived from investigations on large dams, while small low-head dams have been given less attention (Singer & Gangloff, 2011; Thoni et al., 2014; Yan et al.,2013). Although some researchers have found that fish species richness (Tiemann et al., 2004) and assemblage structure (Raborn & Schramm, 2003) in the dammed segments did not differ from free-flowing segments, others observed that lowhead dams may substantially reduce local fish species richness (Dodd et al., 2003) and alter fish assemblage structure (Gillette et al., 2005; Poulet, 2007). These differences in results may be associated with dam size and location. Substantial modifications in fish assemblages may occur only in the impoundments immediately upstream, but not downstream of the dams (Yan et al., 2013). Compared with free-flowing stream segments,impoundments created by low-head dams are characterized with slower flows, deeper and wider water bodies, and smaller substrates (Gillette et al., 2005; Tiemann et al., 2004). Such local habitat modifications may alter fish assemblages by decreasing the numbers of lotic species and increasing the numbers of lentic species (Gillette et al., 2005; Tiemann et al.,2004; Yan et al., 2013). Moreover, multiple low-head dams upstream and/or downstream may cumulatively affect local habitat and fish assemblages (Cumming, 2004; Helfrich et al.,1999; Wang et al., 2011). Effects of impoundment are likely to increase with downstream flow past consecutive dams because river transport is largely unidirectional (Santucci et al.,2005).

    We hypothesize that the fish assemblages in the impoundments of low-head dams are influenced by size of dams, number of dams upstream and/or downstream, local habitat conditions, and tributary position in the stream network. However, to our knowledge, the combined influences of local habitat, tributary position, and low-head dam characteristics on fish assemblages have not been thoroughly examined. Chu et al. (2015b) collected fishes from 62 impoundments created by low-head dams in headwater streams of the Qingyi River, China. After classifying the 25 fish species collected into 12 indigenous (naturally inhabiting in lotic headwater streams) and 13 nativeinvading species (naturally preferring lentic or slow-flowing waters of mid to lower reaches of a river network), the authors assessed the influence of abiotic (local habitat) and biotic (native invader) factors on the indigenous fish assemblages. However, they did not examine how the entire fish assemblages,indigenous and native-invasive fishes together, related to abiotic factors. In this study, we used the data of Chu et al.(2015b) to examine relationships between abiotic factors and fish assemblages in the 62 impoundments. Our aims were: (1)to determine the pure and combined effects of three groups of environmental factors (i.e., local habitat, tributary position, and dam characteristic) on fish species richness; (2) to determine the pure and combined effects of these environmental factors on fish species composition; (3) and to assess the relative importance of the three groups of environmental factors influencing local species richness and species composition.

    MATERIALS AND METHODS

    Study area

    The Qingyi River originates in the northern portion of Huangshan Mountain and flows northeast toward its confluence with the lower Yangtze River, China. As a result of a subtropical monsoon climate, this basin is characterized by asymmetric seasonal temperature and precipitation distributions. Monthly mean temperature ranges from -2.1 oC in January to 27.5 oC in July and approximately 79% of the annual rainfall occurs from April to September. Approximately 1 000 low-head dams have been built on the tributaries of this basin for agricultural irrigation, resident water consumption, and recreational fishing (Chu et al., 2015b; Yan et al., 2011, 2013).

    Fish sampling

    A total of 62 impoundments created by low-head dams within the first-order (defined from the Anhui Province topographic maps of 1: 300 000 scales using the method of Strahler (1957))headwater streams were sampled once during October and November 2011. Each sampled impoundment was selected in the field based on criteria that dam height was less than 4 m and impoundment water depth was less than 1 m. Only one site of 50 m long was sampled within each impoundment; however,when impoundments were less than 50 m long, the entire impoundments were sampled. Fish were collected using a backpack electrofishing gear (CWB-2000 P, China; 12 V import and 250 V export) by wading in two passes without blocking nest. Each electrofishing pass was operated with a uniform sampling effort (approximately 30 min sampling time for each 50 m sampling segment) by the same three persons, one operating the gear and the other two capturing fishes. Fish were identified in the field to species, counted, and returned to the sampling sites alive.

    Environmental survey

    We characterized local habitat conditions of each sampled impoundment by eight habitat variables, including wetted width (m), water depth (m), water temperature (oC), dissolved oxygen (mg/L), conductivity (mS/s), current velocity (m/s), and substrate coarseness and heterogeneity. Wetted width was measured along five transects equally spacing across the stream channel. Water depth, water temperature, dissolved oxygen, and conductivity were measured at four equal interval points along each transect (JENCO 6350, 9010, USA). Current velocity was taken at 60% of water depth at each point (FP111,USA). Substrate was quantified with a 1 m lead core dividedinto 10 cm sections, using the frequency size class method of Bain (1999). Mean and standard deviation of dominant substrate values were regarded as indices of substrate coarseness and heterogeneity, respectively.

    We quantified the dam characteristics of each sampled impoundment by two groups of dam variables, including dam size and dam numbers. Dam size consisted of the height (m), length (m)and area (m2) of each low-head dam surveyed. Dam height was estimated as the vertical distance from the natural streambed at the downstream toe of the dam to the lowest point on the dam crest. Dam length was measured as the horizontal distance across channel at the dam crest. Then, dam area was calculated from its height and length, by approximation to a half ellipse. Dam number involved the numbers of upstream and downstream dams for each impoundment surveyed. Because each surveyed impoundment was located at the first-order headwater stream, dam number upstream was counted as the number of all dams (including lowhead dams and hydropower stations) upstream of each sampling site along each surveyed headwater stream. Dam number downstream was counted in terms of all dams downstream of each surveyed low-head dam along the mainstem of the Qingyi River before it flows into the Yangtze River.

    The impoundments sampled were all located in the first-order streams, suggesting that both stream order (Strahler, 1957) and stream link magnitude (Shreve, 1966) of all tributaries surveyed amounted to one. So, according to Yan et al. (2011), we quantified other two variables (confluence link and downstream link) to describe the tributary position of each impoundment within the Qingyi basin network. Confluence link is the number of confluences downstream from each segment (Fairchild et al.,1998), and downstream link is the linkage number of the stream segment that the sampling stream segment immediately flowing into (Osborne & Wiley, 1992). The two variables were assigned to each segment sampled using Anhui Province topographic maps (1: 300 000 scales).

    Data analysis

    We used stepwise regression to evaluate the effects of environmental variables on fish species richness (Legendre & Legendre, 1998). First, we built three regression models to determine the effects of local habitat alone, tributary position alone, and dam characteristics alone on fish species richness. We entered 10 habitat variables, two tributary variables, and five dam variables into the three regression models,respectively. Second, we entered all the 17 explanatory variables measured into one regression model to identify the combined effects of the three groups of environmental factors on fish species richness. Because only one significant predictor variable was screened out for all the four models, we did not use Akaike's Information Criterion (AIC) to select the optimal model for explaining the variance in fish species richness any more. Prior to analysis, fish and environment data were logtransformed to meet the assumptions of normality and homogeneity of variances. We used the SPSS 13.0 statistics package to perform statistical analysis, and statistical significance was accepted at P<0.05.

    Using CANOCO 4.5 software package (ter Braak & Verdonschot 1995), we performed a redundancy analysis (RDA)to evaluate the variations in species composition in relation to environmental variables. We used RDA instead of CCA in the relationship analysis because detrended correspondence analyses indicated that our fish data set had a short gradient length (a measure of species turnover) for which the linear model of RDA was more appropriate than CCA (ter Braak & Verdonschot 1995). Similar to our regression analysis, we performed three RDAs to assess the correlations between fish species composition and local habitat alone, tributary position alone, and dam variables alone, respectively; then, we performed one RDA to determine how the three groups of environmental factors affected jointly fish species composition. These analyses included the relative abundances of all fish species except that occurring at two sites or fewer to avoid biased weighting. All the variables entered the analysis after a forward selection procedure, showing their importance in explaining the total variability in species composition. The significance (P<0.05) of the RDA gradient was assessed by Monte Carlo permutation tests and their importance measured by the eigenvalues of the first two axes (ter Braak & Verdonschot 1995). All fish and environment data were log10(X+1) transformed to meet assumptions of multivariate normality and to moderate the influence of extreme data.

    RESULTS

    Species richness

    When the three groups of environmental variables were considered separately, our results showed that fish species richness was related negatively to substrate heterogeneity (local habitat), and confluence link (tributary position), and positively related to number of upstream dams (dam characteristic) (P<0.05). The number of dams upstream explained the most variability (55%) and substrate heterogeneity explained the least variability (30%) in species richness (Table 1). However, when the combined effects of the three groups of factors on fish species richness were considered, only the number of upstream dams explained species richness (P<0.05),whereas local habitat and tributary position variables were less important (P>0.05) (Table 1).

    Table 1 Linear regression models of fish species richness versus local habitat, tributary position, and dam characteristic

    Species composition

    When the three groups of environmental variables were considered separately, substrate heterogeneity (local habitat)(Figure 1A), confluence link (tributary position) (Figure 1B), and dam height and numbers of dams upstream and downstream (dam characteristic) (Figure 1C) were significantly related to species composition (P<0.05). These variables explained 55.6% (substrate heterogeneity), 57.0% (confluence link) and 32.0% (dam characteristics) of the variance of species composition, respectively. When combining local habitat,tributary position, and dam characteristic together, the key factors influencing species composition included substrate coarseness and heterogeneity, confluence link, and dam area (P<0.05) (Figure 1D).

    Different species responded differently to environmental variables. As substrate heterogeneity increased, abundances of Vanmanenia stenosoma, Cobitis rarus and Acrossocheilus fasciatus increased and Carassius auratus, Opsarrichthys bidens and Odontobutis obscura decreased (Figure 1A). When confluence link increased, C. rarus and A. fasciatus became more abundant and Abbottina rivularis, Pseudorasbora parva,Rhodeus ocellatus, Hemiculter leucisculus and O. obscura became less abundant (Figure 1B). As the number of upstream and downstream dams declined, the number of O. bidens, A. rivularis, R. ocellatus and P. parva increased whereas V. stenosoma, A. fasciatus and Pseudogobio vaillanti decreased. As dam height increased, Zacco platypus, Cobitis sinensis and C. rarus increased, whereas P. vaillanti and Ctenogobius spp. decreased (Figure 1C). When the combined effects of the three groups of factors on fish species composition were considered,substrate heterogeneity and confluence link showed positive correlations with the first RDA axis, and substrate coarseness and dam area negatively related to the second RDA axis (Figure 1D).

    Figure 1 Redundancy analysis (RDA) diagrams for fish species composition and local habitat (A), tributary position (B), dam characteristic (C) and their combinations (D) in the impoundments created by low-head dams

    DISCUSSION

    In this study, we found that fish species richness in impoundments behind low-head dams of the Qingyi River was related to substrate heterogeneity, confluence link, and dam number upstream, and fish species composition was influenced by substrate heterogeneity, confluence link, dam height, dam numbers upstream and downstream. Dam characteristics like number of dam upstream were more important in affecting species richness but less important in determining fish species composition than local habitat like substrate heterogeneity and tributary position like confluence link.

    Substrate provides the prerequisite micro-conditions for many stream fishes and can be viewed as an indicator of stream habitat quality (Bain, 1999). Substrate coarseness and heterogeneity, representing substrate size and microhabitatdiversity, may substantially influence stream fish assemblages (Matthews, 1998). The positive relationship between substrate heterogeneity and fish species richness in the free-flowing segments of streams have been observed by many researchers (e.g., Gorman & Karr, 1978; Gratwicke & Sperght, 2005; Li et al.,2014; Wang et al., 2013). However, we found that fish species richness in the impoundments behind low-head dams was negatively related to substrate heterogeneity. This discrepancy may be associated with the difference in environmental conditions and fish species compositions between impoundments and free-flowing segments. Compared with free-flowing segments, impoundments behind low-head dams are characterized by slower flows, deeper water and finer substrate,and by less endemic lotic fishes and more widespread lentic fishes (Gillette et al., 2005; Tiemann et al., 2004; Yan et al,2013). The total of 25 fish species collected in this study included 12 indigenous specialist species naturally inhabiting upland streams, and 13 invasive generalist species naturally preferring lowland waters (Chu et al., 2015b). Although species richness of indigenous species is positively related to substrate heterogeneity (Chu et al., 2015b), our redundancy analysis showed that the abundances of most invasive species, such as C. auratus, P. parva, A. rivularis, M. anguillicaudatus, R. ocellatus and O. obscura, were negatively related to substrate heterogeneity. Therefore, the habitat-generalist characteristics of invasive fishes in impoundments could lessen the positive correlation between substrate heterogeneity and fish species richness observed elsewhere.

    Fluvial systems have interconnected network architectures with complex but definable 'network geometry' (Fausch et al.,2002; Wiens, 2002) or “dendritic ecosystem network” (Grant et al., 2007). At a river network scale, local fish assemblages are determined by tributary position within a watershed network (Grenouillet et al., 2004; Yan et al., 2011), because the rates of fish immigration and emigration influence local fish assemblages in streams and depend on tributary position (Robinson & Rand, 2005; Taylor & Warren, 2001). This may explain why some adventitious streams, defined as streams at least three stream orders smaller than that into which they flow,often hold more diverse fish assemblages than headwater streams with similar size to adventitious streams (Hitt & Angermeier, 2008; Osborne & Wiley, 1992). We found that both species richness and fish assemblages were significantly related to confluence link, suggesting that fish movements may influence fish assemblages within the impoundments by low-head dams. Others have revealed that some variables on tributary position, such as downstream link (Grenouillet et al., 2004; Osborne & Wiley,1992;) and confluence link (Li et al., 2014; Smith & Kraft,2005) influence local fish assemblages in free-flowing segments.

    We found that both fish species richness and composition in impoundments were related to the number of dams upstream and/or downstream, suggesting of cumulative effects of multiple dams on fish assemblages. These cumulative effects have been also observed by other researchers such as Helfrich et al. (1999), Cumming (2004), and Wang et al. (2011). Because river transport is largely unidirectional, effects of impoundment often increase with downstream flow past consecutive dams (Santucci et al., 2005). Our redundancy analysis showed that the abundances of most indigenous species were negatively related to the number of dams upstream, but the opposite was observed for invasive species. Similarly, in the same study area,Chu et al. (2015b) found that local species richness of indigenous fishes correlated negatively with the number of dams upstream, while the richness of invasive fishes correlated positively with the number of upstream dams. Therefore,multiple impoundments behind low-head dams may cumulate effects on local fish assemblages, negatively impacting indigenous fishes but benefiting invasive species. In addition,we also found that fish species composition in impoundments was related to dam height and dam area. This is consistent with the opinion that the magnitude of dam effects and the degree to which local habitat conditions and fish assemblages are impacted depend on dam size, because dam size influences the size of their impoundments (March et al., 2003; Poff & Hart,2002).

    The relative importance of different environmental variables in determining fish assemblages may depend on many factors,such as spatial scale at which an investigation is conducted (Jackson et al., 2001; Wang et al., 2006), features of environmental conditions in a particular region (Hughes et al.,2015; Wang et al., 2006), and indicator used to describe fish assemblages (species richness v.s. species composition) (Li et al., 2014; Yan et al., 2011). We demonstrated that dam characteristics (i.e., dam number upstream) were more important in affecting fish species richness in impoundments than local habitat (i.e., substrate heterogeneity) and tributary position (i.e., confluence link). By modifying local habitat features, low-head dams and other co-occurring anthropogenic activities (e.g., land use and water pollution) decrease local species richness, alter the longitudinal pattern of fish species richness along upstream-downstream gradient, and lessen the effects of habitat factors on local species richness (Chu et al.,2015a). In addition, by blocking fish passage, dams also constrain fish movements among stream segments and lower the effects of tributary position on fish species richness (Yan et al.,2011). However, we also demonstrated that dam characteristic was less important in influencing fish species composition than habitat and tributary position. This suggests that the relative abundances of those fish species may depend more on species habitat preferences and stream size than on impoundment size and number (Yan et al., 2011).

    REFERENCES

    Bain MB. 1999. Substrate. In: Bain MB, Stevenson NJ. Aquatic Habitat Assessment: Common Methods. Bethesda MD: American Fisheries Society,95-103.

    Chu L, Wang WJ, Yan LL, Yan YZ, Zhu R, Si C. 2015a. Fish assemblages and longitudinal patterns in the headwater streams of the Chencun Reservoir in the Huangshan Area. Acta Ecologica Sinica, 35(3): 900-910. (in Chinese)

    Chu L, Wang WJ, Zhu R, Yan YZ, Chen YF, Wang LZ. 2015b. Variation infish assemblages across impoundments of low-head dams in headwater streams of the Qingyi River, China: effects of abiotic factors and native invaders. Environmental Biology of Fishes, 98(1): 101-112.

    Cumming GS. 2004. The impact of low-head dams on fish species richness in Wisconsin, USA. Ecological Applications, 14(5): 1495-1506.

    Dauwalter DC, Splinter DK, Fisher WL, Marston RA. 2008. Biogeography,ecoregions, and geomorphology affect fish species composition in streams of eastern Oklahoma, USA. Environmental Biology of Fishes, 82(3): 237-249.

    Dodd HR, Hayes DB, Baylis JR, Carl LM, Goldstein JD, McLaughlin RL,Noakes DLG, Porto LM, Jones ML. 2003. Low-head sea lamprey barrier effects on stream habitat and fish communities in Great Lakes basin. Journal of Great Lakes Research, 29(Suppl 1): 386-402.

    Fairchild GW, Horwitz RJ, Nieman DA, Boyer MR, Knorr DF. 1998. Spatial variation and historical change in fish communities of the Schuylkill River drainage, Southeast Pennsylvania. The American Midland Naturalist,139(2): 282-295.

    Fausch KD, Torgersen CE, Baxter CV, Li HW. 2002. Landscapes to riverscapes: bridging the gap between research and conservation of stream fishes. Bioscience, 52(6): 483-498.

    Gillette DP, Tiemann JS, Edds DR, Wildhaber ML. 2005. Spatiotemporal patterns of fish assemblage structure in a river impoundment by low-head dams. Copeia, 2005(3): 539-549.

    Gilliam JF, Fraser DF, Alkins-Koo M. 1993. Structure of a tropical stream fish community: a role for biotic interactions. Ecology, 74(6): 1856-1870.

    Gorman OT, Karr JR. 1978. Habitat structure and stream fish communities. Ecology, 59(3): 507-515.

    Grant EHC, Lowe WH, Fagan WF. 2007. Living in the branches: population dynamics and ecological process in dendritic networks. Ecology Letters,10(2): 165-175.

    Gratwicke B, Speight MR. 2005. The relationship between fish species richness, abundance and habitat complexity in a range of shallow tropical marine habitats. Journal of Fish Biology, 66(3): 650-667.

    Grenouillet G, Pont D, Hérissé C. 2004. Within-basin fish assemblage structure: the relative influence of habitat versus stream spatial position on local species richness. Canadian Journal of Fisheries and Aquatic Sciences,61(1): 93-102.

    Harding JS, Benfield EF, Bolstad PV, Helfman GS, Jones EBD. 1998. Stream biodiversity: The ghost of land use past. Proceedings of the National Academy of Sciences of the United States of America, 95(25): 14843-14847.

    Harvey BC, Stewart AJ. 1991. Fish size and habitat depth relationships in headwater streams. Oecologia, 87(3): 336-342.

    Helfrich LA, Liston C, Hiebert S, Albers M, Frazer K. 1999. Influence of lowhead diversion dams on fish passage, community composition, and abundance in the Yellowstone River, Montana. Rivers, 7(1): 21-32.

    Hitt NP, Angermeier PL. 2008. Evidence for fish dispersal from spatial analysis of stream network topology. Journal of the North American Benthological Society, 27(2): 304-320.

    Hoeinghaus DJ, Winemiller KO, Birnbaum JS. 2007. Local and regional determinants of stream fish assemblage structure: inferences based on taxonomic vs. functional groups. Journal of Biogeography, 34(2): 324-338.

    Hughes RM, Herlihy AT, Sifneos JC. 2015. Predicting aquatic vertebrate assemblages from environmental variables at three multistate geographic extents of the western USA. Ecological Indicators, 57: 546-556.

    Jackson DA, Peres-Neto PR, Olden JD. 2001. What controls who is where in freshwater fish communities: the role of biotic, abiotic, and spatial factors. Canadian Journal of Fisheries and Aquatic Sciences, 58(1): 157-170.

    Legendre P, Legendre L. 1998. Numerical Ecology. 2nded. Amsterdam: Elsevier.

    Li YH, Yan YZ, Zhu R, Zhou K, Chu L, Wan A, Wang XS. 2014. Spatial variations in fish assemblages within the headwater streams of the Wanhe watershed: A river network-based approach. Journal of Fishery Sciences of China, 21(5): 988-999. (in Chinese)

    March JG, Benstead JP, Pringle CM, Scatena FN. 2003. Damming tropical island streams: problems, solutions, and alternatives. BioScience, 53(11): 1069-1078.

    Matthews WJ. 1998. Patterns in Freshwater Fish Ecology. New York: Kluwer Academic Press.

    Murchie KJ, Hair KPE, Pullen CE, Redpath TD, Stephens HR, Cooke SJ. 2008. Fish response to modified flow regimes in regulated rivers: research methods, effects and opportunities. River Research and Applications, 24(2): 197-217.

    Nilsson C, Reidy CA, Dynesius M, Revenga C. 2005. Fragmentation and flow regulation of the world’s large river systems. Science, 308(5720): 405-408.

    Osborne LL, Wiley MJ. 1992. Influence of tributary spatial position on the structure of warmwater fish communities. Canadian Journal of Fisheries and Aquatic Sciences, 49(4): 671-681.

    Ostrand KG, Wilde GR. 2001. Temperature, dissolved oxygen, and salinity tolerances of five prairie stream fishes and their role in explaining fish assemblage patterns. Transactions of the American Fisheries Society,130(5): 742-749.

    Poff NL, Hart DD. 2002. How dams vary and why it matters for the emerging science of dam removal. BioScience, 52(8): 659-668.

    Poff NL, Zimmerman JKH. 2010. Ecological responses to altered flow regimes: a literature review to inform the science and management of environmental flows. Freshwater Biology, 55(1): 194-205.

    Poulet N. 2007. Impact of weirs on fish communities in a piedmont stream. River Research and Applications, 23(9): 1038-1047.

    Raborn SW, Schramm HL Jr. 2003. Fish assemblage response to recent mitigation of a channelized warmwater stream. River Research and Applications, 19(4): 289-301.

    Robinson JL, Rand PS. 2005. Discontinuity in fish assemblages across an elevation gradient in a southern Appalachian watershed, USA. Ecology of Freshwater Fish, 14(1): 14-23.

    Rosenberg DM, Berks F, Bodaly RA, Hecky RE, Kelly CA, Rudd JWM. 1997. Large-scale impacts of hydroelectric development. Environmental Reviews, 5(1): 27-54.

    Rosenberg DM, McCully P, Pringle CM. 2000. Global-scale environmental effects of hydrological alterations. BioScience, 50(9): 746-751.

    Santucci VJ Jr, Gephard SR, Pescitelli SM. 2005. Effects of multiple lowhead dams on fish, macroinvertebrates, habitat, and water quality in the Fox River, Illinois. North American Journal of Fisheries Management, 25(3): 975-992.

    Shreve RL. 1996. Statistical law of stream numbers. The Journal of Geology, 74(1): 17-37.

    Singer EE, Gangloff MM. 2011. Effects of small dam on freshwater mussel growth in an Alabama (U.S.A.) stream. Freshwater Biology, 56(9): 1904-1915.

    Smith TA, Kraft CE. 2005. Stream fish assemblages in relation to landscape position and local habitat variables. Transactions of the American Fisheries Society, 134(2): 430-440.

    Strahler AN. 1957. Quantitative analysis of watershed geomorphology. Transactions-American Geophysical Union, 38(6): 913-920.

    Taylor CM, Warren ML Jr. 2001. Dynamics in species composition of stream fish assemblages: environmental variability and nested subsets. Ecology, 82(8): 2320-2330.

    ter Braak CJF, Verdonschot PFM. 1995. Canonical correspondence analysis and related multivariate methods in aquatic ecology. Aquatic Sciences,57(3): 255-289.

    Thoni R, Hocomb J, Nichols R, Gangloff MM. 2014. Effects of small dams on sunfish assemblages in North Carolina piedmont and coastal plain streams. Transactions of the American Fisheries Society, 143(1): 97-103. Tiemann JS, Gillette DP, Wildhaber ML, Edds DR. 2004. Effects of lowhead dams on riffle-dwelling fishes and macroinvertebrates in a Midwestern river. Transactions of the American Fisheries Society, 133(3): 705-717.

    Vila-Gispert A, García-Berthou E, Moreno-Amich R. 2002. Fish zonation in a Mediterranean stream: Effects of human disturbances. Aquatic Sciences,64(2): 163-170.

    Wang LZ, Seelbach PW, Hughes RM. 2006. Introduction to landscape influences on stream habitats and biological assemblages. American Fisheries Society Symposium, 48(48): 1-23.

    Wang LZ, Infante D, Lyons J, Stewart J, Cooper A. 2011. Effects of dams in river networks on fish assemblages in non-impoundment sections of river in Michigan and Wisconsin, USA. River Research and Applications, 27(4): 473-487.

    Wang LZ, Lyons J, Rasmussen P, Seelbach P, Simon T, Wiley M, Kanehl P,Baker E, Niemela S, Stewart PM. 2003. Watershed, reach, and riparian influences on stream fish assemblages in the Northern Lakes and Forest Ecoregion, U.S.A. Canadian Journal of Fisheries and Aquatic Sciences,60(5): 491-505.

    Wang WJ, Chu L, Si C, Zhu R, Chen WH, Chen FM, Yan YZ. 2013. Spatial and temporal patterns of stream fish assemblages in the Qiupu Headwaters National Wetland Park. Zoological Research, 34(4): 417-428. (in Chinese)

    Wiens JA. 2002. Riverine landscapes: Taking landscape ecology into the water. Freshwater Biology, 47(4): 501-515.

    Yan YZ, He S, Chu L, Xiang XY, Jia YJ, Tao J, Chen YF. 2010. Spatial and temporal variation of fish assemblages in a subtropical small stream of the Huangshan Mountain. Current Zoology, 56(6): 670-677.

    Yan YZ, Wang H, Zhu R, Chu L, Chen YF. 2013. Influences of low-head dams on the fish assemblages in the headwater streams of the Qingyi watershed, China. Environmental Biology of Fishes, 96(4): 495-506.

    Yan YZ, Xiang XY, Chu L, Zhan YJ, Fu CZ. 2011. Influences of local habitat and stream spatial position on fish assemblages in a dammed watershed,the Qingyi Stream, China. Ecology of Freshwater Fish, 20(2): 199-208.

    10.13918/j.issn.2095-8137.2016.2.67

    Appendix I Species composition, code, and classification (indigenous v.s. invasive) of fishes in 62 impoundments surveyed

    Continued

    Appendix II Summary statistic for explanatory variables measured for local habitat, tributary position, and dam characteristics

    20 October 2015; Accepted: 15 January 2016

    Foundation items: This work was supported by grants from the Natural Science Foundation of China (NSFC 31172120, 31372227, 31500452)

    *Corresponding author, E-mail: yanyunzhi7677@126.com

    九九久久精品国产亚洲av麻豆| 亚洲成人久久爱视频| 日日啪夜夜撸| 少妇 在线观看| 2018国产大陆天天弄谢| 麻豆久久精品国产亚洲av| 又黄又爽又刺激的免费视频.| tube8黄色片| 国产一级毛片在线| 水蜜桃什么品种好| 亚洲精品影视一区二区三区av| 国产成人免费观看mmmm| 亚洲精品亚洲一区二区| 伦理电影大哥的女人| 亚洲精品乱码久久久v下载方式| 欧美高清性xxxxhd video| 国产视频内射| 成年免费大片在线观看| 日韩一区二区三区影片| 欧美激情在线99| 亚洲内射少妇av| 日韩制服骚丝袜av| 亚洲第一区二区三区不卡| 九草在线视频观看| 日韩电影二区| 下体分泌物呈黄色| 禁无遮挡网站| 简卡轻食公司| 深爱激情五月婷婷| 日韩欧美 国产精品| 免费人成在线观看视频色| 简卡轻食公司| 在线观看免费高清a一片| 亚洲成人精品中文字幕电影| 成年版毛片免费区| 水蜜桃什么品种好| 国精品久久久久久国模美| 国产精品国产三级国产av玫瑰| 寂寞人妻少妇视频99o| 国产精品一区二区性色av| 国产色婷婷99| 免费观看的影片在线观看| 成人漫画全彩无遮挡| 亚洲成人精品中文字幕电影| 午夜日本视频在线| 成年女人看的毛片在线观看| 亚洲av二区三区四区| 秋霞伦理黄片| 别揉我奶头 嗯啊视频| 最近最新中文字幕免费大全7| 成人黄色视频免费在线看| 插逼视频在线观看| 久久亚洲国产成人精品v| 国产日韩欧美亚洲二区| 97精品久久久久久久久久精品| 国产精品伦人一区二区| 亚洲色图综合在线观看| 亚洲欧美日韩卡通动漫| 少妇猛男粗大的猛烈进出视频 | av在线观看视频网站免费| 亚洲一区二区三区欧美精品 | a级一级毛片免费在线观看| 九九爱精品视频在线观看| 大香蕉97超碰在线| 国产精品爽爽va在线观看网站| 偷拍熟女少妇极品色| 成人漫画全彩无遮挡| 免费电影在线观看免费观看| 精品久久久久久电影网| 成人高潮视频无遮挡免费网站| 伊人久久精品亚洲午夜| 伊人久久精品亚洲午夜| 免费av观看视频| 岛国毛片在线播放| 色吧在线观看| 久久国产乱子免费精品| 在线看a的网站| 婷婷色麻豆天堂久久| 男的添女的下面高潮视频| 日韩成人伦理影院| 国产在线男女| 精品一区二区三卡| 波多野结衣巨乳人妻| 国产伦精品一区二区三区四那| 18禁动态无遮挡网站| 黄色视频在线播放观看不卡| 国产成人aa在线观看| 晚上一个人看的免费电影| 美女高潮的动态| 午夜精品国产一区二区电影 | 久久精品夜色国产| 五月天丁香电影| 日韩 亚洲 欧美在线| 在线免费观看不下载黄p国产| 午夜爱爱视频在线播放| 老司机影院成人| 插阴视频在线观看视频| 国产高清国产精品国产三级 | 国产午夜福利久久久久久| 亚洲成色77777| 色综合色国产| 白带黄色成豆腐渣| 国产白丝娇喘喷水9色精品| 夫妻性生交免费视频一级片| 精品熟女少妇av免费看| 午夜福利在线观看免费完整高清在| 制服丝袜香蕉在线| 亚洲精品乱码久久久久久按摩| 男女边摸边吃奶| 亚洲欧美日韩无卡精品| 狂野欧美激情性xxxx在线观看| 一级毛片我不卡| 18禁动态无遮挡网站| 中文资源天堂在线| 亚洲av欧美aⅴ国产| 亚洲av中文av极速乱| 欧美区成人在线视频| 嫩草影院入口| 女人十人毛片免费观看3o分钟| 国产av国产精品国产| 好男人在线观看高清免费视频| 久久久久国产精品人妻一区二区| 亚洲精品中文字幕在线视频 | 亚洲最大成人av| 国产免费视频播放在线视频| 欧美成人a在线观看| 亚洲最大成人手机在线| 最近的中文字幕免费完整| 国产精品一区www在线观看| 免费看av在线观看网站| 免费黄频网站在线观看国产| 伦精品一区二区三区| 国产白丝娇喘喷水9色精品| 国产永久视频网站| 2022亚洲国产成人精品| 日韩不卡一区二区三区视频在线| 久久久精品94久久精品| 最近中文字幕高清免费大全6| 嫩草影院入口| 在线免费观看不下载黄p国产| 精品人妻一区二区三区麻豆| 在线播放无遮挡| 亚洲经典国产精华液单| 日韩一本色道免费dvd| 亚洲国产av新网站| 国产黄a三级三级三级人| 午夜免费鲁丝| 国产亚洲精品久久久com| 国产乱来视频区| 亚洲av成人精品一区久久| 日韩,欧美,国产一区二区三区| 成人毛片60女人毛片免费| 蜜臀久久99精品久久宅男| 日韩大片免费观看网站| a级毛片免费高清观看在线播放| 成人漫画全彩无遮挡| 高清欧美精品videossex| 少妇熟女欧美另类| 极品教师在线视频| 中文字幕免费在线视频6| 看黄色毛片网站| 波野结衣二区三区在线| 日韩国内少妇激情av| 人妻 亚洲 视频| 亚洲人成网站高清观看| 国产日韩欧美亚洲二区| 久久精品国产鲁丝片午夜精品| 免费黄频网站在线观看国产| 久久久精品免费免费高清| 久久鲁丝午夜福利片| 免费大片黄手机在线观看| av.在线天堂| 91午夜精品亚洲一区二区三区| 亚洲av免费在线观看| 99久久中文字幕三级久久日本| 久久久精品94久久精品| 久久久久久久午夜电影| 性插视频无遮挡在线免费观看| 国产久久久一区二区三区| 五月开心婷婷网| 国产一区二区在线观看日韩| 久久ye,这里只有精品| 51国产日韩欧美| 国产在线男女| 黄片wwwwww| 99久国产av精品国产电影| av在线亚洲专区| 99久久精品热视频| 最近2019中文字幕mv第一页| 欧美日韩综合久久久久久| av一本久久久久| 国产乱来视频区| 人人妻人人爽人人添夜夜欢视频 | 大码成人一级视频| 免费在线观看成人毛片| tube8黄色片| 最近中文字幕2019免费版| 亚洲av免费在线观看| 久久国内精品自在自线图片| 国产欧美日韩精品一区二区| 97人妻精品一区二区三区麻豆| 一区二区三区四区激情视频| 中文字幕人妻熟人妻熟丝袜美| .国产精品久久| 久久久久久久久大av| 亚洲婷婷狠狠爱综合网| 国产免费又黄又爽又色| 国内少妇人妻偷人精品xxx网站| 少妇的逼好多水| 国产 精品1| 秋霞伦理黄片| 精品人妻视频免费看| 亚洲av电影在线观看一区二区三区 | 午夜免费鲁丝| 久久精品国产亚洲av天美| 一个人看的www免费观看视频| 国产精品久久久久久精品电影| 一本久久精品| 99久久精品一区二区三区| 久久久亚洲精品成人影院| 噜噜噜噜噜久久久久久91| 麻豆精品久久久久久蜜桃| 亚洲在久久综合| eeuss影院久久| 精品久久久久久久末码| 夜夜爽夜夜爽视频| 国产高潮美女av| 久久久久久国产a免费观看| 亚洲精品成人av观看孕妇| 日韩成人伦理影院| 2021天堂中文幕一二区在线观| 久久综合国产亚洲精品| 欧美成人午夜免费资源| 国产成人精品久久久久久| 一级片'在线观看视频| 亚洲欧美一区二区三区国产| 国产伦在线观看视频一区| 欧美亚洲 丝袜 人妻 在线| 在线观看美女被高潮喷水网站| 又爽又黄无遮挡网站| 99re6热这里在线精品视频| 最新中文字幕久久久久| 热99国产精品久久久久久7| 男人添女人高潮全过程视频| 2021天堂中文幕一二区在线观| 超碰av人人做人人爽久久| 美女视频免费永久观看网站| 亚洲国产精品999| 日本色播在线视频| 精品国产乱码久久久久久小说| 性色av一级| 亚洲精品成人av观看孕妇| 热re99久久精品国产66热6| 日日啪夜夜爽| 22中文网久久字幕| 免费观看性生交大片5| 高清毛片免费看| 最近中文字幕2019免费版| 中文精品一卡2卡3卡4更新| 亚洲人与动物交配视频| 国产成人精品福利久久| 我的女老师完整版在线观看| 99热6这里只有精品| 亚洲在久久综合| 少妇丰满av| 亚洲国产最新在线播放| 成人综合一区亚洲| 2021天堂中文幕一二区在线观| 亚洲色图综合在线观看| 在线观看一区二区三区激情| 2021天堂中文幕一二区在线观| 嫩草影院新地址| 欧美高清性xxxxhd video| 日本免费在线观看一区| 丰满乱子伦码专区| 久久久久久久大尺度免费视频| 三级男女做爰猛烈吃奶摸视频| 97超视频在线观看视频| 少妇熟女欧美另类| 国产午夜精品一二区理论片| 欧美日韩视频精品一区| 日日摸夜夜添夜夜爱| 午夜精品国产一区二区电影 | 免费高清在线观看视频在线观看| 成人漫画全彩无遮挡| 欧美极品一区二区三区四区| 精品国产一区二区三区久久久樱花 | 国产精品蜜桃在线观看| 久久久久国产网址| 亚洲精品色激情综合| 性色av一级| 欧美最新免费一区二区三区| 国产亚洲91精品色在线| 男人和女人高潮做爰伦理| 成人高潮视频无遮挡免费网站| 久久久成人免费电影| 性色avwww在线观看| 国产精品国产av在线观看| 久久精品国产自在天天线| 能在线免费看毛片的网站| 嫩草影院精品99| 亚洲av在线观看美女高潮| 天堂中文最新版在线下载 | 男男h啪啪无遮挡| 亚洲无线观看免费| 又粗又硬又长又爽又黄的视频| 精品一区二区三区视频在线| 欧美一级a爱片免费观看看| 自拍偷自拍亚洲精品老妇| 在线观看免费高清a一片| 青春草视频在线免费观看| 中文字幕av成人在线电影| 国产精品久久久久久av不卡| 欧美3d第一页| 18+在线观看网站| 精品久久久久久久久av| 国产淫语在线视频| 色吧在线观看| 久久精品国产鲁丝片午夜精品| 精华霜和精华液先用哪个| 久久人人爽人人片av| 中文天堂在线官网| 水蜜桃什么品种好| 日韩av在线免费看完整版不卡| 久久久久网色| 永久免费av网站大全| 99久久精品国产国产毛片| 国产白丝娇喘喷水9色精品| 亚洲色图综合在线观看| 黄色一级大片看看| 一二三四中文在线观看免费高清| 看免费成人av毛片| 色播亚洲综合网| 日韩国内少妇激情av| 美女xxoo啪啪120秒动态图| 波多野结衣巨乳人妻| 九色成人免费人妻av| 99热这里只有是精品50| 国产亚洲91精品色在线| 亚洲丝袜综合中文字幕| 麻豆国产97在线/欧美| 国产成人a区在线观看| 最近最新中文字幕免费大全7| 亚洲精品一区蜜桃| 久久久成人免费电影| 欧美成人午夜免费资源| 少妇人妻久久综合中文| av在线app专区| 亚洲欧美成人综合另类久久久| 中文字幕制服av| 婷婷色综合大香蕉| 九九爱精品视频在线观看| 久久久久精品久久久久真实原创| 亚洲久久久久久中文字幕| 99热国产这里只有精品6| 女的被弄到高潮叫床怎么办| 亚洲欧洲国产日韩| 精品亚洲乱码少妇综合久久| 国产精品久久久久久精品电影| 久久精品国产亚洲av天美| 国产伦精品一区二区三区视频9| 在线亚洲精品国产二区图片欧美 | 日日啪夜夜爽| 一本色道久久久久久精品综合| 新久久久久国产一级毛片| 国产精品秋霞免费鲁丝片| 久久精品国产亚洲av天美| 日韩不卡一区二区三区视频在线| av在线app专区| av免费在线看不卡| 成人综合一区亚洲| 国产国拍精品亚洲av在线观看| 大又大粗又爽又黄少妇毛片口| 又粗又硬又长又爽又黄的视频| 联通29元200g的流量卡| 亚洲国产欧美人成| 久久久欧美国产精品| 亚洲最大成人av| 日韩成人伦理影院| 国产黄片视频在线免费观看| 亚洲经典国产精华液单| 亚洲欧美清纯卡通| 大话2 男鬼变身卡| 久久久久国产精品人妻一区二区| 亚洲精品,欧美精品| 女人被狂操c到高潮| 亚洲成人中文字幕在线播放| 中文字幕亚洲精品专区| 美女国产视频在线观看| 亚洲av成人精品一区久久| 大码成人一级视频| 国产在线男女| 观看美女的网站| 国产欧美亚洲国产| 最后的刺客免费高清国语| 亚洲国产高清在线一区二区三| 男插女下体视频免费在线播放| 高清午夜精品一区二区三区| 在线免费十八禁| 欧美精品一区二区大全| 99热这里只有是精品在线观看| 欧美日韩在线观看h| 18禁动态无遮挡网站| 少妇人妻 视频| 又爽又黄a免费视频| 一级毛片 在线播放| 最近最新中文字幕大全电影3| xxx大片免费视频| av专区在线播放| 噜噜噜噜噜久久久久久91| 中国美白少妇内射xxxbb| 国产高清国产精品国产三级 | 婷婷色综合大香蕉| 97在线人人人人妻| 国产精品一及| 久久精品熟女亚洲av麻豆精品| 精品久久国产蜜桃| 欧美日本视频| 免费观看性生交大片5| 亚洲色图av天堂| 插阴视频在线观看视频| 午夜福利高清视频| 亚洲精品中文字幕在线视频 | 夫妻性生交免费视频一级片| 在现免费观看毛片| 国产极品天堂在线| 久久久久久久大尺度免费视频| 亚洲国产av新网站| 联通29元200g的流量卡| 深爱激情五月婷婷| 黄色日韩在线| 老司机影院成人| 亚洲av中文av极速乱| 成人二区视频| 日本wwww免费看| 99热这里只有是精品50| 亚洲最大成人av| 日韩,欧美,国产一区二区三区| 18禁在线无遮挡免费观看视频| 国产有黄有色有爽视频| 国产黄色视频一区二区在线观看| av播播在线观看一区| 成年av动漫网址| 搡女人真爽免费视频火全软件| 国产色爽女视频免费观看| 久久人人爽人人爽人人片va| av在线亚洲专区| 色播亚洲综合网| 免费观看av网站的网址| 日韩 亚洲 欧美在线| av播播在线观看一区| av免费在线看不卡| 国产探花在线观看一区二区| 久久综合国产亚洲精品| 三级男女做爰猛烈吃奶摸视频| 男人和女人高潮做爰伦理| 日韩av不卡免费在线播放| 国产精品久久久久久精品古装| 亚洲欧洲国产日韩| 成人综合一区亚洲| 一级毛片久久久久久久久女| 一个人看的www免费观看视频| 国内精品宾馆在线| 亚洲精品,欧美精品| 熟妇人妻不卡中文字幕| 国产成人精品婷婷| 欧美激情国产日韩精品一区| 一个人观看的视频www高清免费观看| 欧美日韩一区二区视频在线观看视频在线 | 精品国产一区二区三区久久久樱花 | 丝袜美腿在线中文| 国产av码专区亚洲av| 免费观看的影片在线观看| 亚洲一区二区三区欧美精品 | 国产成人免费观看mmmm| 久久久精品免费免费高清| 午夜免费鲁丝| 熟女电影av网| 精品人妻熟女av久视频| 深夜a级毛片| 乱码一卡2卡4卡精品| 国产欧美另类精品又又久久亚洲欧美| 精品久久久噜噜| 99九九线精品视频在线观看视频| av天堂中文字幕网| 51国产日韩欧美| 欧美bdsm另类| 大又大粗又爽又黄少妇毛片口| 国产精品女同一区二区软件| 三级男女做爰猛烈吃奶摸视频| 国产精品一区www在线观看| 国产精品无大码| 涩涩av久久男人的天堂| 国产高清国产精品国产三级 | 菩萨蛮人人尽说江南好唐韦庄| 国产免费又黄又爽又色| 一级二级三级毛片免费看| 免费av不卡在线播放| 水蜜桃什么品种好| 又大又黄又爽视频免费| 国产欧美日韩精品一区二区| 欧美zozozo另类| 三级国产精品欧美在线观看| 女人被狂操c到高潮| 99久久中文字幕三级久久日本| 久久久欧美国产精品| 毛片一级片免费看久久久久| 日韩欧美 国产精品| 如何舔出高潮| 国产欧美另类精品又又久久亚洲欧美| 国产成人一区二区在线| 最后的刺客免费高清国语| 亚洲精品亚洲一区二区| 久久精品国产a三级三级三级| 2018国产大陆天天弄谢| 久久久久国产网址| 在线免费十八禁| 亚洲精品久久久久久婷婷小说| 久久久久国产精品人妻一区二区| 肉色欧美久久久久久久蜜桃 | 久久6这里有精品| 欧美激情国产日韩精品一区| 色视频在线一区二区三区| 国产又色又爽无遮挡免| 国产精品精品国产色婷婷| 欧美高清成人免费视频www| 夫妻午夜视频| 人人妻人人看人人澡| 美女xxoo啪啪120秒动态图| 特级一级黄色大片| 久久影院123| 欧美+日韩+精品| 色播亚洲综合网| 夫妻性生交免费视频一级片| 18禁裸乳无遮挡免费网站照片| 久久久久久久久久人人人人人人| 嫩草影院新地址| 色综合色国产| 久久午夜福利片| av福利片在线观看| 日韩欧美精品免费久久| 精品国产一区二区三区久久久樱花 | 国产午夜精品一二区理论片| xxx大片免费视频| 老师上课跳d突然被开到最大视频| 五月伊人婷婷丁香| 久久久久久久大尺度免费视频| 91aial.com中文字幕在线观看| 国产乱来视频区| 国产亚洲5aaaaa淫片| 人妻系列 视频| 亚洲天堂av无毛| 久久久a久久爽久久v久久| 少妇裸体淫交视频免费看高清| 你懂的网址亚洲精品在线观看| 欧美3d第一页| 大片电影免费在线观看免费| 精品酒店卫生间| 久久精品夜色国产| 国产成人免费观看mmmm| 在线精品无人区一区二区三 | tube8黄色片| 亚洲精品久久午夜乱码| 边亲边吃奶的免费视频| 国产久久久一区二区三区| 激情 狠狠 欧美| 99精国产麻豆久久婷婷| 成人鲁丝片一二三区免费| 在线观看三级黄色| 五月开心婷婷网| 秋霞在线观看毛片| 爱豆传媒免费全集在线观看| 成人高潮视频无遮挡免费网站| 黄色视频在线播放观看不卡| www.色视频.com| 亚洲,欧美,日韩| 老司机影院成人| 亚洲欧洲国产日韩| 日韩成人伦理影院| 在线 av 中文字幕| 男女下面进入的视频免费午夜| 国产精品国产av在线观看| 亚洲综合精品二区| 美女主播在线视频| 午夜免费观看性视频| 欧美成人a在线观看| 只有这里有精品99| 亚洲三级黄色毛片| 国产成人a∨麻豆精品| 男人舔奶头视频| 国产精品麻豆人妻色哟哟久久| 免费观看无遮挡的男女| 日韩av不卡免费在线播放| 最近最新中文字幕大全电影3| 国产高清有码在线观看视频| 91午夜精品亚洲一区二区三区| 国产日韩欧美亚洲二区| 亚洲av一区综合| 国产爱豆传媒在线观看| 乱码一卡2卡4卡精品| 免费观看性生交大片5| 男女啪啪激烈高潮av片| 久久精品国产鲁丝片午夜精品| 美女xxoo啪啪120秒动态图| 永久免费av网站大全| 又爽又黄a免费视频| 免费观看性生交大片5| 亚洲av中文av极速乱| 美女国产视频在线观看| 欧美变态另类bdsm刘玥| 亚洲四区av| 深夜a级毛片| 久热这里只有精品99| 性色avwww在线观看| 精品久久久久久久久亚洲|