Translator Disclaimer
1 September 2016 Quantitative Monitoring of Freshwater Mussel Populations from 1979–2004 in the Clinch and Powell Rivers of Tennessee and Virginia, with Miscellaneous Notes on the Fauna
Author Affiliations +

The Clinch and Powell rivers, Tennessee (TN) and Virginia (VA), upstream of Norris Reservoir, TN, are known for high freshwater mussel species diversity and endemism. Collectively, these rivers harbored at least 56 species historically and 49 are extant, many of which now survive only in the Clinch or Powell rivers or a few other streams. Among an unparalleled 24 federally endangered mussel species known from these rivers, 20 species are considered extant. We sampled 0.25 m-2 quadrats at six Clinch River sites and four Powell River sites for a total of 4–6 sample years at each site. Overall trends were highly significant in the Clinch River, with mean mussel density at combined sites in each state increasing from 16.5 m-2 to 41.7 m-2 (p < 0.0001) at sites in TN but declining from 12.0 m-2 to 3.3 m-2 (p < 0.001) at sites in VA. Cumulative species richness was 39, ranging from 36 in TN to 27 in VA. Greater density in the Clinch River, TN, was due primarily to increases in Epioblasma capsaeformis, Medionidus conradicus, and Ptychobranchus subtentus, which were rare or undetected at most sites in 1979, but increased five- to ten-fold by 2004. Conversely, at Pendleton Island, VA, which was the best site for mussels in the river circa 1980, the decline in density was highly significant, from 24.6 m-2 in 1979 to 4.6 m-2 (p < 0.001) in 2004. In the Powell River, there was also a highly significant decline in mean mussel density at combined sites from 8.7 m-2 to 3.3 m-2 (p < 0.001), with a total of 33 species documented. Though species diversity remains relatively high, our results confirm that mussel populations have declined in large reaches of each river over the 25-year study period.


The Clinch River and its largest tributary Powell River are located in northeastern TN and southwestern VA and are part of the upper Tennessee River drainage (Figure 1). The Tennessee River drainage supports the highest freshwater mussel diversity of any comparably-sized river system in the world. More than 105 species are known from this drainage, with at least 36 species endemic to it or shared only with the Cumberland River drainage (Parmalee and Bogan 1998). Collectively, upland portions of these two drainages are known as the Tennessee-Cumberland Province (Haag 2010). Mussel diversity was highest in the mainstem Tennessee River and its large tributaries, but impoundments created during the 1920s through 1970s destroyed most large-river habitats (Haag 2009). The lower Clinch River was impounded by Watts Bar Dam on the Tennessee River, and Melton Hill and Norris dams on the Clinch River (river km [RKM] 37.0 and 128.5, respectively). Norris Dam impounds the river to about river km 249 as well as the lower 90 km of the Powell River, and the dam effectively isolated these two rivers and eradicated at least 10 additional species from the drainage (Ortmann 1918; Ahlstedt 1991a). Nevertheless, the free-flowing upper reaches of the Clinch and Powell rivers are among the most important remaining riverine habitats in the Tennessee River drainage, and they support a large percentage of the surviving mussel fauna of the region (Johnson et al. 2012; Jones et al. 2014).

Figure 1.

The Clinch and Powell river watersheds showing locations of sites (in RKM) sampled from 1979–2004.


Among the 56 species known historically from the Clinch and Powell river mainstems upstream of Norris Reservoir, 24 are now federally endangered under the Endangered Species Act (ESA), though 4 of these listed species are considered extinct or extirpated from these rivers (Table 1). Further, an additional seven of the extant species are included in a petition for possible federal listing. The Clinch River harbors the largest remaining population (namely, Dromus dromas, Epioblasma brevidens, E. capsaeformis, Fusconaia cor, F. cuneolus, Hemistena lata, Ptychobranchus subtentus, Quadrula cylindrica strigillata), or one of the few existing populations (e.g., Cyprogenia stegaria, E. florentina aureola, Lemiox rimosus, Pegias fabula, Pleurobema plenum, Q. sparsa, Venustaconcha trabalis [studies by Kuehnl (2009) and Lane et al. (2016) have shown that Villosa trabalis belongs in the genus Venustaconcha, and that Villosa perpurpurea is a synonym; see Discussion]), of 15 endangered mussels, in addition to large populations of several other imperiled species (Jones et al. 2014; Table 1). Fifteen of 19 endangered species are considered extant in the Powell River, which itself harbors 1 of only 2 extant populations of D. dromas, Q. cylindrica strigillata, Q. intermedia, and Q. sparsa (Johnson et al. 2012).

Various malacologists have reported on the mussels in the Clinch and Powell rivers over the last century. Arnold E. Ortmann (1918), Carnegie Museum, Pittsburgh, Pennsylvania, reported the only systematic pre-impoundment collection records in the study area, including several records from Adams (1915). In the 1960s and 1970s, David H. Stansbery, Ohio State University Museum of Biological Diversity, Columbus, Ohio, and his students made scores of collections in the study area, documenting declines in species richness since Ortmann's (1918) collections, many from areas now inundated by Norris Reservoir (Stansbery 1973). Greater survey effort and interest in conserving the mussel fauna accelerated in the mid-1970s following passage of the ESA in 1973. These surveys include the Clinch River (Stansbery 1973; Bates and Dennis 1978; Stansbery et al. 1986; Dennis 1989; Ahlstedt 1991a; Church 1991; Jones et al. 2014), the Powell River (Ahlstedt and Brown 1979; Dennis 1981; Ahlstedt 1991b; Wolcott and Neves 1994; Johnson et al. 2012), or both rivers (Neves et al. 1980; Dennis 1985; Ahlstedt and Tuberville 1997).

Table 1.

Scientific names, and federal and Freshwater Mollusk Conservation Society (FMCS; J.D. Williams, Florida Museum of Natural History, unpub. data) status of mussel species known from the Clinch and Powell river mainstems upstream of Norris Reservoir in TN and VA. √ = extant and sampled during our study, √x = extant but not sampled or recognized during our study, * = very rare, - = no federal status, CS = currently stable, E = endangered, EX = extirpated, FE = federally endangered, NR = not reported, P = petitioned for federal listing, RI = sampled during our study and subsequently considered extirpated but now extant from reintroduction, T = threatened, V = vulnerable, and X = extinct. Species list and study area status updated from Johnson et al. (2012) and Jones et al. (2014).




The goal of our study was to quantify changes in the mussel fauna of the upper Clinch and Powell rivers over a 25-y period (1979-2004). Our primary objective was to quantitatively sample multiple fixed sites in both rivers and evaluate species richness, density and population trends during this period. Secondary objectives were to: 1) compare our results with previous and more recent collection data, 2) compile a comprehensive list of mussels known from the study area and their conservation status, and 3) generate a timeline of anthropogenic impacts that have potentially affected the status of the fauna during the past and into the future.


Study Area

The watersheds of the Clinch River and its tributary Powell River form a large portion of the headwaters of the upper Tennessee River drainage in northeastern TN and southwestern VA (Figure 1). These drainages occur primarily in the Ridge and Valley Physiographic Province, with a small portion in the Appalachian Plateaus Physiographic Province in VA. The study area incorporates the free-flowing mainstems of these rivers upstream of Norris Reservoir, TN. The upper Clinch River watershed contains an area of 3,721 km2, while the upper Powell River watershed contains 2,471 km2. Land cover is primarily agriculture and mixed forest, with small towns scattered in the drainages and fossil fuel extraction in the Appalachian Plateaus headwaters. Industry is limited, but two coal-fired power plants are located on the upper Clinch River.

Site Selection and Sampling Methodology

We selected sampling sites during float surveys via canoe and small watercraft in 1979 (Ahlstedt 1991a, b; Table 2; Figure 1). Selected sites had aggregations of mussels in shoals—habitat patches having shallow water and swift flows over primarily gravel and cobble substrates—that also offered easy access. We identified sampling sites by RKM and landmarks on 7.5-minute topographic maps. We initially selected 11 sites on the Clinch River and 15 sites on the Powell River (Ahlstedt and Tuberville 1997). However, due to severe mussel declines at some sites, as well as time and funding constraints, sampling sites were reduced to six in the Clinch River (three each in TN and VA) and four in the Powell River (three in TN and one in VA) for data analyses.

Quantitative mussel sampling was conducted by randomly placing 0.25 m2 quadrats on substrate in the shoal habitat of each site. Using mask and snorkel, surveyors searched for mussels by excavating substrate from quadrats to a depth of ∼15 cm or until hardpan or bedrock was reached. Once live mussels were identified and recorded, we returned them to the substrate. Over the 25-y period, we conducted four (at Pendleton Island, VA) or five (at all other sites) sampling events at each Clinch River site, and six sampling events at each Powell River site (Table 3; Appendices I and II).

Data Analysis

We calculated mean density for each species and the assemblage at each site and year of sampling (Table 3; Appendices I and II). The 1979 quadrat data from all sites in the Clinch and Powell rivers were not available for analysis, only the mean values per site were available for that year, which were previously recorded by Ahlstedt and Tuberville (1997). Hence, all analyses were restricted to mean density values per site and year. We used a generalized linear model (GLM) to test for significance of trends in mean density of the mussel assemblage over time to make four comparisons: 1) sites in the Clinch River, VA; 2) sites in the Clinch River, TN; 3) Pendleton Island, VA; and 4) sites in the Powell River, TN and VA (Figure 2). We implemented the GLM using a Poisson distribution and log link function in the program R (R Development Core Team 2006) and test results were considered significant at α=0.05. Mean density values of the portion of our study from 1979–1994 were reported by Ahlstedt and Tuberville (1997). Mean mussel density at Pendleton Island in 1987 was obtained from Dennis (1989), who used similar sampling methods as our study.

Table 2.

Location and quadrat sample sizes of the ten long-term fixed-station monitoring sites for mussels m the Clinch and Powell rivers, TN and VA, sampled from 1979–2004.


Table 3.

Mussels per meter squared, number of species, number of endangered species, mean values and associated 95% confidence intervals (CI) for sampling sites in the Clinch and Powell rivers, TN and VA, sampled from 1979–2004. Non-overlapping CI's among sites in each respective river are significantly different at the 0.05 alpha level. Numbers in parentheses under each site location are the total number of species collected at the site over the study.




Conservation Status of the Fauna

We compiled a comprehensive list of mussels known from the upper Clinch and Powell river mainstems based on published literature and other records (Table 1). This list includes the population status of each species in the study area, federal status under the U.S. Fish and Wildlife Service (USFWS), and its global conservation status according to the Freshwater Mollusk Conservation Society (FMCS) (J.D. Williams, Florida Museum of Natural History, unpub, data). Finally, we generated a chronology of anthropogenic impacts from the literature and our personal observations over the last 40 y likely affecting the status of the mussel fauna (Table 4).


Clinch River

At the six study sites, we observed a total of 39 of 55 mussel species (71 %) known from the Clinch River mainstem upstream of Norris Reservoir (Table 1; Appendix I). Species richness ranged from 36 in TN to 27 in VA, and among sites from 31 at Kyles Ford, TN, to 17 at Semones Island, VA. Over the sampling period, richness declined from 34 in 1979 to 29 in 2004 (Table 3). No other site yielded as many species during any intervening sampling year as did Kyles Ford, though richness dropped from 27 in 1979 to 23 species in both 1999 and 2004. Species richness increased from 11 to 17 species at Swan Island, TN, and 15 to 20 species at Brooks Island, TN, from 1979 to 2004. Sites in VA had lower species richness relative to those in TN, with the exception of Pendleton Island, VA, where 21 species were recorded in 1979. However, species richness declined to a low of 10 species at this site in 1999. At Speers Ferry, VA, species richness fluctuated from a high of 13 in 1988 to a low of 9 in 1999, and similarly at Semones Island from a high of 14 in 1988 to a low of 6 in 1999. Mussel diversity in Clinch River included 16 federally endangered species—14 in TN and 8 in VA. Endangered species ranged from 12 (Kyles Ford) to 8 (Swan Island) in TN and 8 (Speers Ferry) to 5 (Semones Island) in VA.

Mean mussel density among all sites combined on the TN side of the Clinch River increased significantly (p < 0.001) from 16.5 m-2 in 1979 to 41.7 m-2 in 2004 (Figure 2A). Density at the beginning and end of our study ranged from 7.0 to 29.4 m-2 at Swan Island, 11.4 to 21.3 m-2 at Brooks Island, and 31.0 to 74.3 m-2 at Kyles Ford, respectively, though the increasing trend was not uniform over all sampling periods (Table 3). Conversely, mean mussel density at sites on the VA side decreased significantly (p < 0.001) from 12.0 m-2 in 1979 to 3.3 m-2 in 2004 (Figure 2B). Over this period, density essentially remained unchanged at Speers Ferry (3.7 m-2) but declined significantly (p < 0.001) at Pendleton Island from 24.6 to 4.6 m-2 (Figure 2C) and also declined at Semones Island from 7.7 to 1.7 -2 (Table 3).

Figure 2.

Time series plots and linear regression analyses of mean mussel density from 1979–2004 in reaches and sites in the Clinch and Powell rivers of TN and VA; data were collected using a random survey design. The mean density value of 18.7 mussels m-2 at Pendleton Island in 1987 was from data collected by Dennis (1989); data shown in panels B and C. Reported p-value indicates significance of the mussel density and year sampled trend.


Among species, Actinonaias pectorosa and A. ligamentina dominated overall abundance in the Clinch River at sites in both states (Appendix I). The next three most abundant species in VA were Elliptio dilatata, Fusconaia subrotunda, and Medionidus conradicus, while in TN they were M. conradicus, Ptychobranchus subtentus, and Epioblasma capsaeformis. Ptychobranchus subtentus was by far the most abundant endangered species reported, and was fourth in overall abundance. Peak densities of this species reached 20.3 m-2 in 1999 and 16.2 m-2 in 2004 at Kyles Ford. By 2004, the species had become more common at the two other TN sites (>3.0 m-2 per sample) but remained uncommon at VA sites (<0.3 m-2 per sample). Other relatively common listed species (∼1 m-2 per sample) by the end of our study were E. capsaeformis at all three TN sites, Dromus dromas at Swan Island, and E. triquetra at Brooks Island.

A total of 55 species are known historically from the Clinch River and we consider 48 species to be extant, including 20 of 24 federally endangered species (Table 1). Overall, 39 of the extant species in the river are imperiled. The USFWS has been petitioned to list under the ESA seven imperiled species known from and considered extant in the river.

Powell River

At the four sites, we observed a total of 33 of 47 mussel species (70%) known from the mainstem Powell River upstream of Norris Reservoir (Table 1; Appendix II). Species richness was 26 in 1979 but declined to 14 by 2004; among sites, it ranged from 24 at Buchanan Ford, TN, to 19 at Bales Ford, TN (Table 3). Between 1979 and 2004, richness declined from 16 to 7 species at both McDowell Shoal, TN, and Fletcher Ford, VA, and from 12 to 6 species at Bales Ford. At Buchanan Ford the decline was 14 to 11 species. Powell River diversity included 12 endangered species, where each site had eight endangered species except Bales Ford (7 endangered species).

Mean mussel density among all sites combined declined significantly (8.8 to 3.2 m-2; p < 0.001) over the study period (Figure 2D) and was most severe at Fletcher Ford (11.2 to 1.4 m-2; Appendix II). Only at Buchanan Ford and Fletcher Ford did density ever exceed 10 m-2, but decades ago in 1979 and 1983. By 2004, density ranged from 1.4 to 2.2 m-2 among sites, except at Buchanan Ford where it remained comparatively high at 8.0 m-2. Declines were steep at other sites over 25 y, varying from 69% at McDowell Shoal to 88% at Fletcher Ford (Table 3; Appendix II).

Table 4.

Chronology of some significant perturbations that have occurred in the Clinch and Powell rivers.




Actinonaias pectorosa and A. ligamentina were also the co-dominant species in the Powell River, though their densities over the study averaged only 2.0 m-2 and 1.6 m-2 per sample, respectively (Appendix II). Medionidus conradicus, Fusconaia subrotunda, and Elliptio dilatata were next in abundance, but relatively uncommon, averaging <0.6 m-2 per sample. Endangered species density declined over the 25 y at all sites, and specimens were nearly always uncommon or rare (≤0.4 m-2 per sample). Among these, only Dromus dromas and Plethobasus cyphyus were found at each site, while Epioblasma capsaeformis, F. cuneolus, and Quadrula cylindrica strigillata were not found in quadrats after 1983.

A total of 47 species are known from the Powell River, and we consider 37 species to be extant, including 15 of 19 federally endangered species (Table 1). Overall, 28 of the extant species in the river are imperiled, 4 of which the USFWS has been petitioned to list under the ESA. Two other petitioned species are considered extirpated in the river.


We documented >30 anthropogenic trends, activities, or explicit events that have likely affected the mussel fauna in the study area since the late 1800s (Table 4). They range from general changes in land-use (e.g., widespread logging, coal extraction, railroad construction) and direct exploitation (e.g., pearling, harvest) to catastrophic site-specific incidents (e.g., toxic spills ca. 1970 and 1998 in the Clinch River, VA). Most perturbations are based on the literature or personal communications with agency personnel, while others include personal observations by the authors.


Overview of the Mussel Faunas

A total of 48 of 55 species recorded from the mainstem Clinch River upstream of Norris Reservoir are considered extant, representing a faunal loss of 13% (Table 1). Our total species richness relative to that recorded by Jones et al. (2014) was 39 to 38, who quantitatively observed all 38 species in TN and 26 species in VA during 2004–2009. They sampled at our six sites plus three more sites in VA and seven more sites in TN. Based on this combined sampling over 30 y, we consider Leptodea fragilis, Quadrula intermedia, and Villosa fabalis to be extirpated from the Clinch River, while Epioblasma haysiana, E. lenoir, and E. torulosa gubernaculum are now extinct. All six species likely persisted in the river until the early 1970s to mid-1980s. Though we did not detect Epioblasma florentina aureola during our sampling, we consider it extant in the upper Clinch River mainstem in VA, despite the catastrophic pollution spill in 1998 that killed at least 182 individuals of this critically endangered species (Jones et al. 2001; Schmerfeld 2006; Table 4). We also did not observe Toxolasma lividum—an FMCS vulnerable petitioned species not reported alive for decades—but consider it extant based on shells collected in TN since the mid-1990s (Jones et al. 2014), and it being a small and easily overlooked species that primarily occurs in seldom-sampled stream margins. Pleurobema sintoxia was considered extirpated (Jones et al. 2014), until fresh-dead shells collected from muskrat middens in Hancock County, TN, in 2013 confirmed its continued presence (S.A. Ahlstedt, unpub. data). It is possible that this species has been confused with individuals of P. cordatum or P. plenum over the past few decades.

Other Clinch River records need clarification. Epioblasma stewardsonii was reported erroneously from the Clinch River upstream of Norris Reservoir by Stansbery (1973) (and repeated by Jones et al. 2014) based on an Ortmann (1918) record actually reported from a pre-impoundment site. Though Ortmann (1918) reported both forms of Quadrula cylindrica— the headwater subspecies Q. c. strigillata and the nominate subspecies Q. c. cylindrica (as Q. cylindrica)—from the currently unimpounded upper Clinch River, we do not recognize the occurrence of the nominate subspecies in our study area. Our viewpoint is supported by Stansbery (1973) and USFWS (2004). We accept the federally endangered Leptodea leptodon as part of the study area mussel fauna based on a museum specimen (U.S. National Museum 150158) with the stream of origin missing from the label (only “Scott County, Virginia” appears for a locality). In all likelihood the specimen is from Clinch River (Williams et al. 2008), which represents a new state record for VA. Probably collected in the early 1900s, the species is now extirpated from the study area. Jones et al. (2014) also recognized this specimen but their position was equivocal, stating that it may have been collected from either the Clinch River or North Fork Holston River. Lastly, recent mitochondrial DNA and soft anatomy data has shown that Villosa perpurpurea and Villosa trabalis in the Clinch River are the same species, which makes the former taxon a synonym of the latter taxon based on priority (Lane et al. 2016). Further, these data show that the species actually belongs in the genus Venustaconcha (Kuehnl 2009; Lane et al. 2016). These taxonomic name changes are reflected in our paper accordingly.

A total of 37 of 47 species recorded from the mainstem Powell River upstream of Norris Reservoir are considered extant, representing a 21% faunal loss (Table 1). Johnson et al. (2012) stated that the Powell River had “likely lost one-third of its species” over the last century. Our estimate of decline reflects an optimistic view that several species may continue to exist but at abundance levels difficult to detect, especially by quadrat sampling. For example, Strophitus undulatus was rediscovered in 2013 in Claiborne Co., TN, after a nearly 40-y absence from collections (T. Lane, Virginia Tech, unpub. data). Regardless, based on Johnson et al. (2012) and our study, we consider Lasmigona holstonia, Leptodea fragilis, Pegias fabula, Toxolasma lividum, and Venustaconcha trabalis to be extirpated from the Powell River, and Epioblasma haysiana, E. lenoir, and E. torulosa gubernaculum to be extinct (Table 1). Of note, while L. holstonia likely is extirpated from the mainstem, it still occurs in at least one headwater tributary, South Fork Powell, VA (R.S. Butler, unpub. data). With the exception of L. fragilis (observed only in 1979), most of these species had likely disappeared by the 1960s. Two additional species, Epioblasma lewisii and Villosa fabalis, occurred in the Powell River a century ago (Ortmann 1918), but were reported only from sites inundated by Norris Reservoir. Herein, we report Cyprogenia stegaria for the first time from the Powell River, based on collections made several decades ago at McDowell Shoal but overlooked in previous studies (S.A. Ahlstedt, unpub. data). No additional records of this species are known, indicating that it is likely extirpated from the river.

Another record warrants discussion. We also include Anodontoides ferussacianus in Table 1 based on a record in Ortmann (1918) of two specimens from an unspecified site on Powell River, Lee County, VA, likely collected well over a century ago. Ortmann (1918) considered the record to be unequivocal, indicating he must have personally studied the specimens. The Powell River record has subsequently been overlooked; the genus is not reported anywhere else in the Tennessee River drainage, and it represents another addition to the VA mussel fauna. Since A. ferussacianus is primarily a smaller stream Midwestern species (Watters et al. 2009) with a range well over a thousand river kilometers from the study area, the form from the Powell River is unlikely the same species. The specimens may actually represent A. denigrata from the adjacent upper Cumberland River drainage (located across the drainage divide in Kentucky), or possibly an undescribed species of Anodontoides.

Among the 24 federally listed species historically known upstream of Norris Reservoir in the Clinch River, 19 of them were shared with the Powell River; 20 and 15 listed species, respectively, are considered extant (Table 1). Endangered species now comprise 40-50% of the Clinch and Powell River mussel faunas. Such high levels of endangered species richness are unparalleled among diverse freshwater faunas of North America. The similarity of endangered species richness over time suggests that declines in the two rivers documented over the past century have been roughly parallel, having affected their faunas to similar degrees, though overall species losses are higher in the Powell River (21% vs. 13%; Table 1). About three-quarters of the extant fauna in these rivers are now comprised of imperiled species.

Clinch River Mussel Declines in VA

The decline in mussel density among Clinch River, VA, sites was highly significant over the study period, and species richness also decreased (Table 3; Figure 2B; Appendix I). Precipitous declines by more than 90% were observed at Pendleton Island (highly significant; Figure 2C) and at Semones Island (untested). These two sites occur in the lower half of a 68-km reach considered a “dead-zone” due to a severe decline in mussel density over more than a 30-y period (Jones et al. 2014). Further, if the 2009 data observed at the three VA sites by Jones et al. (2014) are included in the GLM analysis (1979–2009), the declining trend in mussel density over time remains highly statistically significant (J.W. Jones, unpub. data).

The density decline at Pendleton Island observed during our study continues (Figure 2C); sampling in 2009 produced a density of only 0.7 m-2 dropping from 4.6 m-2 in 2004 (Jones et al. 2014). The decline of the mussel fauna at this site is notable for several reasons. In the 1970s the site harbored 46 species, making it arguably the most diverse site in the country at the time (Jones et al. 2014). In 1979, mussel density was second only to Kyles Ford. Species that were once common are now rare (e.g., Actinonaias spp., Cyclonaias tuberculata, Fusconaia subrotunda, Lampsilis ovata). Many of the remaining species are relatively long-lived, and several short-lived species are already extirpated, an indication of recruitment failure. We recorded the short-lived (∼5 y; Haag 2012) Leptodea fragilis at Pendleton Island in 1979 but nowhere in the Clinch River since then, indicating that it is likely extirpated from the site and river.

Declines on the VA side of the Clinch River also were evident among endangered mussels. By 2004, endangered species were very rare, extirpated, or existed at levels difficult to detect using standard quantitative sampling techniques. Three of six listed species we observed at Pendleton Island in 1979—Fusconaia cuneolus, Ptychobranchus subtentus, and Quadrula cylindrica strigillata—were common (1.1–1.3 m-2) at that time, but have not been observed in quantitative samples since 1999. Among listed mussels, only Fusconaia cor was sampled in 2004. The decline of Fusconaia cuneolus at this site is noteworthy, since it was the most common mussel (2.3 m-2) among the endangered species at the site during the 1970s and fourth in relative abundance, comprising 11.6% of the entire mussel assemblage (Dennis 1989). The last record of Quadrula intermedia in the Clinch River was a fresh dead shell at Pendleton Island in 1983 (Ahlstedt 1991a). Further, Epioblasma torulosa gubernaculum was also last observed at this site in 1983 (Jones et al. 2014) and at Kyles Ford during 1973-1975 sampling (Dennis 1985). The Clinch River, VA, also was the final refugium for E. haysiana, last collected as shells in 1970 (R. Muir, U.S. Geological Survey [USGS] retired, pers. comm.) and in 1984 near Cleveland, VA (R.J. Neves, USGS retired, pers. comm.), and one of the last refugia for E. lenoir, last collected as a shell in the 1960s near St. Paul, VA (Haag 2009).

Speers Ferry had the best mussel fauna among VA sites that we studied. Though the mussel assemblage at this site occurs at a moderate density (>3.7 m-2 since 1999), recruitment is evident and density appears to be increasing, last recorded at 5.0 m-2 in 2009 (Jones et al. 2014). Medionidus conradicus was the most common species and the only mussel with a density >1.0 m-2 since 1999. Despite its abundance, this Tennessee-Cumberland province regional endemic species is considered threatened by FMCS and is petitioned for federal listing. The federally endangered Epioblasma brevidens and Ptychobranchus subtentus appear to be increasing in density in recent years, as have Elliptio dilatata and Lampsilis fasciola, though densities for all four species remain low (<0.6 m-2 since 1999). In contrast, the endangered Venustaconcha trabalis was last sampled there in 1988 and now is rare in the upper river mainstem.

Improvement of the Mussel Fauna in the Clinch River, TN

Mean mussel density increased significantly at TN sites in the Clinch River from 1979–2004 (Figure 2A). Several species account for most of the general increase, particularly Actinonaias pectorosa, Medionidus conradicus, and Ptychobranchus subtentus, but also Lampsilis fasciola, P. fasciolaris, and the FMCS endangered and petitioned for listing Fusconaia subrotunda. The latter species is now common (1.4 and 1.7 m-2) at Brooks Island and Kyles Ford, respectively (Appendix I); Clinch River likely represents its largest population rangewide. Densities of some of the rarer endangered species have generally increased, such as Cyprogenia stegaria, Dromus dromas, Epioblasma capsaeformis, and Epioblasma brevidens. Pleurobema rubrum, an FMCS endangered species that also has been petitioned for listing, was not detected during our study. Nevertheless, it remains a rare species in the Clinch River, which represents one of its largest population's rangewide. Several other species have maintained relatively stable abundance levels since 1979, namely A. ligamentina, Cyclonaias tuberculata, and Lampsilis ovata, or have occurred at low densities (<0.5 m-2) and were sporadically observed during our study, such as Lasmigona costata and Amblema plicata.

The population of Epioblasma capsaeformis in the Clinch River has varied tremendously since the 1970s, highlighting how population trends differ within species over time. The species was common during 1973–1975 sampling, representing 34.0% of mussel abundance at Speers Ferry and 17.7% at Kyles Ford (Dennis 1985, 1989). It declined over the next decade and by 1987, Dennis (1987) warned that E. capsaeformis had become “all but extirpated from Speers Ferry and Kyles Ford.” The species remained generally uncommon in the river through the early 1990s while disappearing from several other rivers (e.g., Powell River), prompting its listing as endangered in 1997. Our data show that its population then began to increase appreciably by 2004. By 2009, E. capsaeformis became the second most abundant mussel on the TN side of the Clinch River (Jones et al. 2014), even exceeding abundance levels observed in the mid-1970s. The decline of this and other mussel populations in the mid-1980s may have been initiated by combined effects of a prolonged drought and chronic pollution (Ahlstedt and Tuberville 1997). Environmental conditions may have remained sub-optimal until ca. 1999 when favorable conditions allowed the species to recover (>1.0 m-2).

The TN section of the Clinch River is not without some species losses and declines in density. Notably, Leptodea fragilis and Quadrula intermedia likely were extirpated from this reach by the mid-1970s. Though not collected in our quantitative sampling since 1979, Truncilla truncata was collected from the TN reach during quantitative sampling in 2005 (Jones et al. 2014). The species has either declined drastically since being relatively common circa 1980, or it may survive in habitats infrequently sampled, such as in pools (Ahlstedt 1991a). Species richness, number of listed species, and density at the three TN sites reached their lowest levels in 1988, which was attributed to summer drought conditions from 1983 to 1988 (Ahlstedt and Tuberville 1997).

Decline of the Powell River Mussel Fauna in TN and VA

The downward trend in mussel diversity and abundance in the Powell River has been evident for decades. A century ago, Ortmann (1918) reported the headwater sites in VA to be depauperate, noting that even common species were often absent. Surveys in the 1970s yielded 36–37 species (Ahlstedt and Brown 1979; Dennis 1981; Ahlstedt 1991b), while another study during 1988–1989 recorded 28 species (Wolcott and Neves 1994). The 1970s surveys yielded no mussels at sites in the uppermost Powell River where Ortmann (1918) reported 13 species. Ortmann (1918) reported several imperiled species now considered extirpated from the mainstem (e.g., Lasmigona holstonia, Pegias fabula, Toxolasma lividum, Venustaconcha trabalis; Table 1). Further, if the 2009 data collected from the three TN sites and one VA site by Johnson et al. (2012) are included in the GLM analysis (1979–2009), the declining trend in mussel density over time remains highly statistically significant (J.W. Jones, unpub. data). Collectively, we found 26 species in 1979, but only 14 in 2004 (Appendix II). The trend continues, as is evident in the significant decline in density over our study period (Figure 2D). Mussel density at Buchanan Ford fared better than our other three sites where declines were steep (Table 3; Appendix II).

Species once common in the Powell River have become increasingly rare, including Actinonaias spp. and Medionidus conradicus. Fusconaia subrotunda was once one of the more common and widespread mussels in the river, but it was not collected after 1994 (Appendix II). No species other than these four occurred at densities of >1.0 m-2 dining our sampling regime. Lack of recruitment of these common mussels was noted in the late 1980s (Wolcott and Neves 1994). The FMCS vulnerable Pleuronaia barnesiana, a regional endemic and petitioned species, was also one of the most common species in the 1970s (Dennis 1985), but we found no evidence of it after 1983. Both F. subrotunda and P. barnesiana persist in the river but are rare (Johnson et al. 2012). Quadrula pustulosa is a common, widespread species not detected during our survey; it persists as the rarest of four Quadrula species, and ironically the only one that is not endangered (Johnson et al. 2012; Table 1). Another common species, Strophitus undulatus had not been reported from the river since the 1970s (Ahlstedt and Brown 1979; Dennis 1981) until found in 2013 in TN. Other common and widespread species, including Alasmidonta marginata and Leptodea fragilis, were not observed after 1979, while Truncilla truncata went undetected during our study. Though all three species were considered likely extirpated from the Powell River by Johnson et al. (2012), we believe A. marginata may persist. It is substantially longer-lived than L. fragilis (Watters et al. 2009) indicating that its extirpation would take longer to detect. Similarly, S. undulatus is very sporadic and has been perpetually rare in study area collections. We observed Pleurobema oviforme—a once common but now FMCS threatened regional endemic and petitioned species—only in 1979 and 1988 at Fletcher Ford. The species may persist but essentially at undetectable levels (Johnson et al. 2012).

Federally endangered mussels in the Powell River were always sporadic in occurrence in our quadrat samples, with no single species ever exceeding 0.6 m-2. Dromus dromas, Epioblasma brevidens, and Plethobasus cyphyus represented the most frequently encountered endangered species in our study. We did not observe Hemistena lata, Cumberlandia monodonta, and Lemiox rimosus, though Ahlstedt and Brown (1979) and Dennis (1981) reported these species from three of our sites prior to 1979; recent data suggests that they remain in the river. A relatively fresh dead specimen of the deeplyburied, easily overlooked H. lata was collected at Bales Ford in 1999 (J.W. Jones, unpub. data). A fresh dead specimen of C. monodonta was found during 2008–2009 (Johnson et al. 2012). This species usually occurs under large slab boulders (Stansbery 1967), a habitat type not well represented during our sampling. Lastly, 15 live individuals of L. rimosus were observed at five sites during 2008–2009 (Johnson et al. 2012). We did not observe E. capsaeformis after 1983, and the species was last reported in the river during 1988–1989 sampling upstream of our VA site (Wolcott and Neves 1994). Considered extirpated, it is now being reintroduced to multiple sites in TN and VA (Carey 2013). Quadrula cylindrica strigillata, Q. intermedia, and Q. sparsa were observed sporadically during our study. The population of Q. sparsa in the Powell River represents the only recruiting population known, underscoring its conservation importance. The other five endangered species considered extant—E. triquetra, Fusconaia cor, F. cuneolus, Pleuronaia dolabelloides, and Ptychobranchus subtentus—are very rare in the Powell River (Johnson et al. 2012).

Similar to the upper Clinch River, VA, mussel declines in the Powell River appear to have been driven by anthropogenic perturbations (Table 4). Change in the mussel fauna at McDowell Shoal epitomizes this decline in diversity and abundance. In the mid-1970s, 38 species were reported there, clearly making it the most productive site known in the river (Ahlstedt and Brown 1979, Dennis 1981; Ahlstedt 1991b; S.A. Ahlstedt, unpub. data). A mussel die-off lasting about three years, was reported by Ahlstedt and Jenkinson (1987) while conducting our 1983 sampling regime at this site; it was postulated that a toxic spill could have been the cause (Ahlstedt and Tuberville 1997). Ahlstedt and Jenkinson (1987) noted significant declines of the dominant species at the site, Actinonaias ligamentina, and total mussels sampled in quadrats between 1979 and 1983. Our data indicate that A. ligamentina never again achieved earlier densities. Collectively, we recorded 22 species in quadrats since 1979, but only 15 species since 1994 and 7 species in 2004. Though 17 species were recorded by Johnson et al. (2012) during qualitative sampling during 2008–2009, they found only 5 species in quadrats. Currently, several Powell River sites have higher species richness than McDowell Shoal. Fletcher Ford also has experienced a severe mussel decline since the late 1970s. In 1978, a density of 24.2 m-2 was calculated for the site (Neves et al. 1980). We recorded steady declines since 1979, with density declining to 1.4 m-2 by 2004.

Historical and Persistent Threats

European settlement of the Southern Appalachian Mountains brought with it vast changes to the landscape and its river drainages through logging, coal mining, railroads, and other activities (Eby 1923; Woodward 1936; Caudill 1963; Hibbard and Clutter 1990; Table 4). Riverine impacts and threats to the mussel fauna in the study area were documented a century ago; Ortmann (1918) noted specific activities detrimental to mussels, such as a wood extraction facility in the upper Powell River drainage near Big Stone Gap, VA. The post-impoundment collections made by Stansbery (1973) in the Clinch River clearly reflected a decline in species distribution and richness over the previous half century. Both authors anticipated further declines in the fauna based on trends and their observations.

Numerous perturbations in the study area have resulted in catastrophic impacts to the mussel fauna (Table 4). Some dieoffs were directly attributable to chemical releases and spills (e.g., Cairns et al. 1971; Crossman 1973; Jones et al. 2001; Schmerfeld 2006), whereas others were less discernable (e.g., Ahlstedt and Jenkinson 1987; Jones et al. 2014). The decline of mussels in the Clinch River “dead zone” reach in VA, which includes Semones and Pendleton islands, likely was due to various poorly understood anthropogenic impacts over time (Krstolic et al. 2013; Johnson et al. 2014; Jones et al. 2014; Zipper et al. 2014). This faunal loss falls under the category of Haag's (2012) enigmatic declines, where all species are affected equally, and subsequent abundance of species postimpact is typically a function of pre-impact population size. The decline of the mussel fauna at Pendleton Island— especially the extinction of E. torulosa gubernaculum— represents one of the greatest losses to mussel conservation over the past 35 y. A long history of anthropogenic impacts to habitat quality in the Powell River has taken a similar toll on its fauna (McCann and Neves 1992; Wolcott and Neves 1994).

Natural resource exploitation has a long history in the Southern Appalachians and extraction of fossil fuels has often been implicated directly in mussel declines in the study area and elsewhere (Wolcott and Neves 1994; Ahlstedt and Tuberville 1997; Haag and Warren 2004; Warren and Haag 2005). The production of coal in VA peaked in 1990 and has since been in decline (Virginia Energy Patterns and Trends 2014). Coal mining and secondarily natural gas extraction nevertheless may pose the most significant threat, and spills from active and inactive coal processing waste ponds are common (Hampson et al. 2000; Table 4).

Impacts of coal mining on river fauna were reviewed by Hull et al. (2006). Mine-related pollutants that may impact mussels (e.g., water column ammonia, arsenic and other metals in sediments) were identified in the Clinch and Powell river drainages (Price et al. 2011). Though contaminants have declined in recent decades, total dissolved solids continue to rise in mined watersheds (Zipper et al. 2016). Research indicates that mussel populations were inversely correlated with deposited coal fines (Kitchel et al. 1981). Juvenile mussels tested in Powell River sediments sampled downstream of a coal processing facility had significantly lower survival rates (p = 0.01) than did juveniles tested in sediments from upstream of the facility (McCann and Neves 1992). Periodic heavy metal toxicity may have played a role in the mussel decline observed at McDowell Shoal in the mid-1980s (Ahlstedt and Jenkinson 1987; Ahlstedt and Tuberville 1997). In general, losses in mussel diversity and particularly abundance are greater on the VA side of the Powell River (Johnson et al. 2012), though this is not apparent from data at our single VA site. The prevalence of resource extraction activities in the headwaters—first timber, then fossil fuels— may largely explain this continuing trend, first observed by Ortmann (1918). This phenomenon is mirrored in our data from the VA side of the Clinch River, and its cause may be similarly complex.

Stochasticity becomes an increasing threat to small, fragmented, and declining populations (Lande et al. 2003); many such mussel populations in the Clinch and Powell rivers are vulnerable to extirpation due to the absence of source populations for recolonization (Allendorf and Luikart 2007). Extinction debt models predict that in populations isolated by habitat destruction, even good competitors and abundant species are susceptible to eventual extirpation (Tilman et al. 1994; Hanski and Ovaskainen 2002). After the initial extinction of numerous mussel species in the early to mid-20th Century caused primarily by impoundments and secondarily water pollution in these rivers, a second extinction “wave” in the 21st Century may affect a broader suite of species due to effects from small population size and fragmentation (Haag 2009; Haag and Williams 2013).

Conservation and Population Restoration Efforts

Malacologists and resource managers in the region have written strategies to guide population restoration and conservation in streams like the Clinch and Powell rivers (Cumberlandian Region Mollusk Restoration Committee 2010; USFWS 2014). Culture facilities of the Virginia Department of Game and Inland Fisheries (VDGIF) and Virginia Tech have implemented a recovery program for increasing mussel diversity and abundance in these rivers. Various reintroduction methodologies have been attempted; translocation of adult mussels from large populations is the most cost-effective method for reestablishing historical populations, though density of available source populations is a limiting factor for most species (Carey et al. 2015). Researchers have refined culture methods for juveniles, allowing greater sizes for release and improved survival rates (Hua et al. 2015).

Epioblasma capsaeformis is the focus of concerted population restoration efforts in the upper Clinch River, VA, and Powell River, TN; survival has been high in both localities and evidence of recruitment documented in the Clinch River (Carey et al. 2015). Other endangered species that are being reintroduced or augmented include E. brevidens (Powell River, TN) and Lampsilis abrupta (Clinch River, TN and VA), in addition to several state priority species in VA in the Clinch River (VDGIF, unpub. data). The fortuitous abundance of Clinch River mussels in TN (e.g., E. brevidens, E. capsaeformis, Medionidus conradicus, Ptychobranchus subtentus) is serving as seed stock for most of these efforts and reintroductions elsewhere in the Tennessee River drainage (Hubbs 2016). Reestablishment of endangered species in historical river reaches increases spatial distribution, improves overall conservation status, and represents the primary means by which recovery under the ESA can be achieved (USFWS 2004).

Fewer species have become extirpated in the Clinch and Powell Rivers compared to many other southeastern United States rivers, and most probably did so prior to 1994. There remains the potential to lose additional species in both watersheds through continued downward spiral of small populations of some species, but positive advancements in research, culture, population reintroduction, habitat restoration, and conservation are providing the knowledge necessary to prevent further declines and extirpations. These collective efforts offer tangible hope for the conservation of the extant fauna, and to create a malacological preserve for imperiled species in the Clinch and Powell rivers.


We wish to thank all of the landowners who graciously provided access to our sampling sites over the years and all the individuals at Tennessee Valley Authority, Tennessee Wildlife Resources Agency, and U.S. Geological Survey who assisted in sampling efforts from 1979–2004. The following individuals assisted with field sampling in 1999 and 2004: J. Aliucci, D. Garst, N. Johnson, R. Mair, B. Ostby, and J. Rash (Virginia Tech); R. Biggins, S. Chance, N. Eckert, B. Evans, and S. Hanlon (U.S. Fish and Wildlife Service); M. Pinder, and B. Watson (Virginia Department of Game and Inland Fisheries); Dr. B. Beaty and M. Dougherty (The Nature Conservancy); and C. Isaac, T. Lowe, and Q. Tolliver (Appalachian Technical Services, Inc.). B. Evans, and S. Hanlon (U.S. Fish and Wildlife Service) provided information on coal mining and observations of threats. We especially thank S. Hanlon for preparing Figure 1, and J. Gamer (Alabama Department of Conservation and Natural Resources), Dr. W. Haag (U.S. Forest Service), and Dr. R. Neves (U.S. Geological Survey, retired) for reviewing and providing valuable comments on earlier drafts of the manuscript, and to Dr. T. Watters and two anonymous reviewers for their efforts during the editorial process. The views expressed in this article are the authors' and do not necessarily represent those of the U.S. Fish and Wildlife Service.



Adams CC. 1915. The variations and ecological distribution of the snails of the genus Io. National Academy of Sciences. Volume XII, 2nd Memoir. Google Scholar


Ahlstedt SA. 1991a. Twentieth century changes in the freshwater mussel fauna of the Clinch River (Tennessee and Virginia). Walkerana 5:73–122. Google Scholar


Ahlstedt SA. 1991b. Cumberlandian mollusk conservation program: mussel surveys in six Tennessee Valley streams. Walkerana 5:123–160. Google Scholar


Ahlstedt SA, Brown SR. 1979. The naiad fauna of the Powell River in Virginia and Tennessee. Bulletin of the American Malacological Union 1979:40– 43. Google Scholar


Ahlstedt SA, Jenkinson JJ. 1987. A mussel die-off in the Powell River, Virginia and Tennessee, in 1983. Pages 21–28 in Neves RJ, editor. Proceedings of the workshop on die-offs of freshwater mussels in the United States. Sponsored by U.S. Fish and Wildlife Service and Upper Mississippi River Conservation Committee. Blacksburg: Virginia Polytechnic Institute and State University. Google Scholar


Ahlstedt SA, Tuberville JD. 1997. Quantitative reassessment of the freshwater mussel fauna in the Clinch and Powell Rivers, Tennessee and Virginia. Pages 107–128 in Cummings KS, Buchanan AC, Mayer CA, Naimo TJ. Conservation and management of freshwater mussels II: initiatives for the future. Proceedings of a UMRCC Symposium, 16–18 October 1995, St. Louis, Missouri. Rock Island, Illinois: Upper Mississippi River Conservation Committee. Google Scholar


Allendorf FW, Luikart G. 2007. Conserving Global Biodiversity: Conservation and the Genetics of Populations. Oxford, United Kingdom: Blackwell Publishing. Google Scholar


Angermeier PL, Smoger RA. 1993. Assessment of biological integrity as a tool in the recovery of rare aquatic species. Virginia Department of Game and Inland Fisheries, Richmond. Google Scholar


Bates JM, Dennis SD. 1978. The mussel fauna of the Clinch River, Tennessee and Virginia. Sterkiana 69–70:3–23. Google Scholar


Boëpple JF, Coker RE. 1912. Mussel resources of the Holston and Clinch River, Tennessee and Virginia. U.S. Bureau of Fisheries Document No. 765:3–13. Google Scholar


Cahn AR. 1936. The molluscan fauna of the Clinch River below Norris Dam upon completion of that structure. Pages 1–27 in Three reports dealing with the clam-shell industry of the Tennessee River Valley. Norris, Tennessee: Tennessee Valley Authority. Google Scholar


Cairns J. Jr. , Crossman JS, Dickman KL, Herrick EE. 1971. Chemical plants leave unexpected legacy in two Virginia rivers. Science 198:1015–1020. Google Scholar


Carey CS. 2013. An evaluation of population restoration and monitoring techniques for freshwater mussels in the upper Clinch River, Virginia, and refinement of culture methods for laboratory-propagated juveniles. Master's Thesis. Blacksburg: Virginia Polytechnic Institute and State University. Google Scholar


Carey CS, Jones JW, Butler RS, Hallerman E. 2015. Restoring the endangered Oyster Mussel (Epioblasma capsaeformis) to the upper Clinch River, Virginia: an evaluation of population restoration techniques. Restoration Ecology 23:447–454. Google Scholar


Carriker NE. 1981. Water quality in the Tennessee Valley–1980. Tennessee Valley Authority Report TVA/ONR/WR-81/2. Google Scholar


Caudill HM. 1963. Night Comes to the Cumberlands. Boston, Massachusetts: Little, Brown and Company. Google Scholar


Church GW. 1991. Survey of the family Unionidae in the upper Clinch River and Little River, Virginia. Charlottesville: Virginia Chapter of The Nature Conservancy. Google Scholar


Crossman JS. 1973. The biological recovery of the Clinch River following pollutional stress. Ph.D. Dissertation. Blacksburg: Virginia Polytechnic Institute and State University. Google Scholar


Cumberlandian Region Mollusk Restoration Committee. 2010. Plan for the population restoration and conservation of imperiled freshwater mollusks of the Cumberlandian Region. Asheville, North Carolina: U.S. Department of Interior, Fish and Wildlife Service. Google Scholar


Dennis SD. 1981. Mussel fauna of the Powell River, Tennessee and Virginia. Sterkiana 71:1–7. Google Scholar


Dennis SD. 1985. Distributional analysis of the freshwater mussel fauna of the Tennessee River system, with special reference to possible limiting effects of siltation. Nashville: Report No. 85-2, Tennessee Wildlife Resources Agency. Google Scholar


Dennis SD. 1987. An unexpected decline in populations of the freshwater mussel, Dysnomia (Epioblasma) capsaeformis, in the Clinch River of Virginia and Tennessee. Virginia Journal of Science 38:281–286. Google Scholar


Dennis SD. 1989. Status of the freshwater mussel fauna [at] Pendleton Island Mussel Preserve, Clinch River, Virginia. Sterkiana 72:19–27. Google Scholar


Eby BJ. 1923. The geology and mineral resources of Wise County and the coal bearing portion of Scott County, Virginia. Bulletin of the Virginia Geological Survey 24:1–617. Google Scholar


Haag WR. 2009. Past and future patterns of freshwater mussel extinctions in North America during the Holocene. Pages 107–128 in Turvey ST, editor. Holocene extinctions. Oxford, United Kingdom: Oxford University Press. Google Scholar


Haag WR. 2010. A hierarchical classification of freshwater mussel diversity in North America. Journal of Biogeography 37:12–26. Google Scholar


Haag WR. 2012. North American freshwater mussels: ecology, natural history, and conservation. Cambridge, United Kingdom: Cambridge University Press. Google Scholar


Haag WR, ML Warren Jr. 2004. Species richness and total population size of freshwater mussels in Horse Lick Creek, Kentucky in 2003. Oxford, Mississippi: U.S. Department of Agriculture, Forest Hydrology Laboratory. Google Scholar


Haag WR, Williams JD. 2014. Biodiversity on the brink: an assessment of conservation strategies for North American freshwater mussels. Hydrobiologia 735:45–60 Google Scholar


Hampson PS., Treece MW Jr , Johnson GC, Ahlstedt SA, Connell JF. 2000. Water quality in the upper Tennessee River basin, Tennessee, North Carolina, Virginia, and Georgia 1994–98. U.S. Geological Survey Circular 1205. Google Scholar


Hanski I, Ovaskainen O. 2002. Extinction debt at extinction threshold. Conservation Biology 16:666–673. Google Scholar


Hibbard WR Jr, Clutter TJ. 1990. Virginia coal, an unabridged history. Blacksburg: Virginia Center for Coal and Energy Research, Virginia Polytechnic Institute and State University. Google Scholar


Hickman ME. 1937. A contribution to mollusca of east Tennessee. M.S. Thesis. Knoxville: University of Tennessee. Google Scholar


Hua D, Jiao Y, Neves RJ, Jones JW. 2015. Using PIT tags to assess individual heterogeneity in a mark recapture study of laboratory-reared juveniles of the endangered Cumberlandian combshell (Epioblasma brevidens). Ecology and Evolution 5:1076–1087. Google Scholar


Hubbs, D. 2016. 2015 Annual Mussel Recovery Activity report for Project 7775. Tennessee Wildlife Resources Agency, Camden. Google Scholar


Hull MS, Cherry DS, Neves RJ. 2006. Use of bivalve metrics to quantify influences of coal-related activities in the Clinch River watershed, Virginia. Hydrobiologia 556:341–355. Google Scholar


Johnson GC, Krstolic JL, Otsby BJK. 2014. Influences of water and sediment quality and hydrological processes on mussels in the Clinch River. Journal of the American Water Resources Association 50:878–897. Google Scholar


Johnson MS, Henley WF, Neves RJ, Jones JW, Butler RS, Hanlon SD. 2012. Freshwater mussels of the Powell River, Virginia and Tennessee: abundance and distribution in a biodiversity hotspot. Walkerana: Journal of the Freshwater Mollusk Conservation Society 15:83–98. Google Scholar


Jones J, Ahlstedt S, Ostby B, Beaty B, Pinder M, Eckert N, Butler R, Hubbs D, Walker C, Hanlon S, Schmerfeld J, Neves R. 2014. Clinch River freshwater mussels upstream of Norris Reservoir, Tennessee and Virginia: a quantitative assessment from 2004–2009. Journal of the American Water Resources Association 50:820–836. Google Scholar


Jones JW, Neves RJ, Patterson MA, Good CR, DiVittoria A. 2001. A status survey of freshwater mussel populations in the upper Clinch River, Tazewell County, Virginia. Banisteria 17:20–30. Google Scholar


Kitchel HE, Widlak JC, Neves RJ. 1981. The impact of coal-mining waste on endangered mussel populations in the Powell River, Lee County, Virginia. Richmond: Virginia State Water Control Board. Google Scholar


Krstolic JL, Johnson GC, Ostby BJK. 2013. Water quality, sediment characteristics, aquatic habitat, geomorphology, and mussel population status of the Clinch River, Virginia and Tennessee, 2009–2011. U.S. Geological Survey Data Series 802. Google Scholar


Kuehnl, K.F. 2009. Exploring levels of genetic variation in the freshwater mussel genus Villosa (Bivalvia Unionidae) at different spatial and systematic scales: implications for biogeography, taxonomy, and conservation. Ph.D. Dissertation. Columbus: Ohio State University. Google Scholar


Lande R, Engen S, Sæther B-E. 2003. Stochastic population dynamics in ecology and conservation. Oxford, United Kingdom: Oxford University Press. Google Scholar


Lane TW, Hallerman EM, Jones JW. 2016. Phylogenetic and taxonomic evaluation of extant populations of the endangered Cumberland bean (Villosa trabalis) and purple bean (Villosa perpurpurea). Conservation Genetics 17:1109–1124. Google Scholar


Masnik MT. 1974. Composition, longitudinal distribution, and zoogeography of the fish fauna of the upper Clinch system in Tennessee and Virginia. Ph.D. dissertation. Blacksburg: Virginia Polytechnic Institute and State University. Google Scholar


McCann MT, Neves RJ. 1992. Toxicity of coal-related contaminants to early life stages of freshwater mussels in the Powell River, Virginia. Asheville, North Carolina: U.S. Department of the Interior, Fish and Wildlife Service. Google Scholar


Neves RJ, Pardue GB, Benfield EF, Dennis SD. 1980. An evaluation of endangered mollusks in Virginia. Richmond: Virginia Commission of Game and Inland Fisheries. Google Scholar


O'Bara CJ, Eggleton MA, McAdoo LM, O'Brien SK. 1994. Clinch River biotic assessment part 1: macrobenthic and fish communities. Nashville: Tennessee Wildlife Resources Agency. Google Scholar


Olem H. 1980. Improving water quality of drainage from abandoned deep mines, St. Charles, Virginia. Chattanooga, Tennessee: Tennessee Valley Authority. 34 pp. Google Scholar


Ortmann AE. 1918. The nayades (freshwater mussels) of the upper Tennessee drainage with notes on synonymy and distribution. Proceedings of the American Philosophical Society 77:521–626. Google Scholar


Parmalee PW, Bogan AE. 1998. The freshwater mussels of Tennessee. Knoxville: University of Tennessee Press. Google Scholar


Price JE, Zipper CE, Jones JW, Franck C. 2011. Water and sediment quality in the Clinch and Powell Rivers of Virginia and Tennessee, 1964–2010. Blacksburg: Virginia Polytechnic Institute and State University. Google Scholar


R Development Core Team. 2006. A list of the Comprehensive R Archive Network (CRAN) sites. Available: (February 2015). Google Scholar


Raleigh RF, Bennett DH, Mohn LO, Maughan OE. 1978. Changes in fish stocks after major fish kills in the Clinch River near St. Paul, Virginia. American Midland Naturalist 99:1–9. Google Scholar


Sagona FJ. 1990. Assessing nonpoint pollution sources in the Tennessee Valley region of southwest Virginia. Richmond: Virginia Water Resources Conference, 22–24 April 1990. Google Scholar


Sagona FJ, Carroll TL. 1991. Aerial inventory of land uses and nonpoint pollution sources in the Powell and upper Clinch River watersheds. Chattanooga, Tennessee: Tennessee Valley Authority Report TVA/WR/WQ-91/14. Google Scholar


Schmerfeld J. 2006. Reversing a textbook tragedy. Endangered Species Bulletin 31:12–13. Google Scholar


Stansbery DH. 1967. Observations on the habitat distribution of the naiad Cumberlandia monodonta (Say, 1829). American Malacological Union Annual Reports for 1966:29–30. Google Scholar


Stansbery DH. 1973. A preliminary report on the naiad fauna of the Clinch River in the southern Appalachian Mountains of Virginia and Tennessee (Mollusca: Bivalvia: Unionidae). American Malacological Union Annual Reports for 1972:20–22. Google Scholar


Stansbery DH., Stein CB, Watters GT. 1986. The distribution and relative abundance of unionid mollusks in the Clinch River in the vicinity of Appalachian Power Company's Clinch River Plant at Carbo, Virginia (Clinch River Miles 264–270). Columbus: Ohio State University Research Foundation. Google Scholar


Tennessee Valley Authority. 1978. Flood of spring 1977 in the Tennessee River basin. Knoxville, Tennessee: Division of Water Management Flood Report WM-27-5-1. Google Scholar


Tennessee/Virginia Joint Task Force. 1985. Conserving the unique values of the Clinch and Powell Rivers. Nashville and Richmond: Report to the Governors of Tennessee and Virginia. Google Scholar


Tennessee Wildlife Resources Commission. 1980. Proclamation No. 80-14. Stating that the Clinch River from the Tennessee/Virginia state line (River mile 202.1) downstream to Norris Dam (River mile 79.8) be designated as a mussel sanctuary. Nashville. Google Scholar


The Nature Conservancy. 1992. Clinch Valley Bioreserve strategic plan. Abingdon: Virginia Chapter. Google Scholar


Tilman D, May RM, Lehman CL, Nowak MA. 1994. Habitat destruction and the extinction debt. Nature 371:65–66. Google Scholar


U.S. Environmental Protection Agency. 2002. Clinch and Powell Valley watershed ecological risk assessment. Washington DC: National Center for Environmental Assessment EPA/600/R-011050. Google Scholar


U.S. Fish and Wildlife Service. 2004. Recovery plan for Cumberland Elktoe (Alasmidonta atropurpurea), Oyster Mussel (Epioblasma capsaeformis), Cumberlandian Combshell (Epioblasma brevidens), Purple Bean (Villosa perpurpurea), and Rough Rabbitsfoot (Quadrula cylindrica strigillata). Atlanta, Georgia: U.S. Department of Interior. Google Scholar


U.S. Fish and Wildlife Service. 2014. Imperiled aquatic species conservation strategy for the upper Tennessee River basin. Gloucester, Virginia: U.S. Department of Interior. Google Scholar


Virginia Energy Patterns and Trends. 2014. Blacksburg: Electronic database maintained at Virginia Polytechnic Institute and State University. Available: (February 2015) Google Scholar


Warren ML Jr , Haag WR. 2005. Spatio-temporal patterns of decline of freshwater mussels in the Little South Fork Cumberland River, USA. Biodiversity and Conservation 14:1383–1400. Google Scholar


Watters GT, Hoggarth MA, Stansbery DH. 2008. The Freshwater Mussels of Ohio. Columbus: The Ohio State University Press. Google Scholar


Williams JD, Bogan AE, Garner JT. 2008. Freshwater mussels of Alabama and the Mobile Basin in Georgia, Mississippi, and Tennessee. Tuscaloosa, Alabama: The University of Alabama Press. Google Scholar


Wolcott LT, Neves RJ. 1994. Survey of the freshwater mussels of the Powell River, Virginia. Banisteria 3:3–14. Google Scholar


Woodward HP. 1936. Natural Bridge and Natural Tunnel, Virginia. Journal of Geology 44:604–616. Google Scholar


Zipper CE, Beaty B, Johnson GC, Jones JW, Krstolic J, Ostby BJK, Wolfe W. 2014. Freshwater mussel population status and habitat quality in the Clinch River, Virginia-Tennessee, USA: a featured collection. Journal of the American Water Resources Association 50:807–819. Google Scholar


Zipper CE, Donovan PF, Jones JW, Li J., Price JE, Stewart RE. 2016. Spatial and temporal correspondences among watershed mining, water quality, and freshwater mussel status in an Eastern USA River. Science in the Total Environment 541:603–615.  Google Scholar


Appendix I.

Summary of mussel density in the Clinch River at six sites sampled in TN and VA during quantitative surveys conducted from 1979–2004. NA = data not available or collected.


Appendix II.

Summary of mussel density in the Powell River at four sites sampled in TN and VA during quantitative surveys conducted from 1979–2004.

© Freshwater Mollusk Conservation Society 2016
Steven A. Ahlstedt, Mark T. Fagg, Robert S. Butler, Joseph F. Connell, and Jess W. Jones "Quantitative Monitoring of Freshwater Mussel Populations from 1979–2004 in the Clinch and Powell Rivers of Tennessee and Virginia, with Miscellaneous Notes on the Fauna," Freshwater Mollusk Biology and Conservation 19(2), 1-18, (1 September 2016).
Published: 1 September 2016

Back to Top