.O‘CR-‘-\o".f '.~.-,.. A EFFECTS OF MUNICIPAL AND COPPER MENE DISCHARGES on; MACROMVERTEBRATES m TWO MICHEGAN STREAMS Thesis for the Degree ef M... S: MEG-REGAN SIRE UNSVERSWY. DAVID Z. SKOLASENSKI 1973 ‘C’ LIBRA p '1! MiChigan 3;." 56 University "' V ‘7' 1—. BIN-BING 0? HBAE & SONS’ 8an R'NUERY we. : Um:- "2’ ENDS-“5 .7 ‘3" kWh-Ii; I WWII!!!WHIWIHW 31293 01073 6654 siéb M 0 {fire ABSTRACT EFFECTS OF MUNICIPAL AND COPPER MINE DISCHARGES ON MACROINVERTEBRATES IN TWO MICHIGAN STREAMS BY David Z. Skolasinski The macroinvertebrate pOpulation of two northern Michigan streams was examined during the summer, fall and spring (1971-1972) to detect the influence of cultural effluents (sewage treatment plant effluent and municipal runoff) and c0pper mine discharges on stream organisms. Cultural influences promoted rigorous and unstable stream conditions which resulted in low species diversity. The adverse effect of the mine discharges was minimal when compared to that of the cultural effluent. Diversity in the mine waters was high and not significantly differ- ent from that of an unperturbed area. However, the species assemblage of the unperturbed site tended toward a more intolerant group of organisms. Lower species diversity values during spring months and in stream sections relatively removed from David Z. Skolasinski human influence, suggested that natural environmental conditions placed a recurring stress on organisms in these areas. Low diversities in perturbed areas were partially attributed to these natural stresses. EFFECTS OF MUNICIPAL AND COPPER MINE DISCHARGES ON MACROINVERTEBRATES IN TWO MICHIGAN STREAMS BY 4,4 David Z. Skolasinski A THESIS Submitted to Michigan State University in partial fulfillment of the requirements for the degree of MASTER OF SCIENCE Department of Fisheries and Wildlife 1973 ACKNOWLEDGMENTS I would like to extend my sincere appreciation to Dr. Eugene W. Roelofs for his advice and guidance during the course of this study and to my committee members, Dr. Howard E. Johnson and Dr. T. Wayne Porter, for their review of the manuscript. I also wish to thank Mr. Edward R. Bingham, Mr. John R. Suffron and Mr. William Maxum of the White Pine COpper Company for making this study possible and for their review of the manuscript. Last but not least, I am deeply indebted to all the peOple who assisted me in the field and laboratory work. Support for the research was obtained from a grant extended to Michigan State University by the White Pine COpper Company. ii TABLE OF CONTENTS Page LIST OF TABLES I O O O O O O O O O I O 0 v LIST OF FIGURES O O O O O O O O O O O O Viii INTRODUCTION 0 O O O O O O O O I O I I 1 DESCRIPTION OF STUDY AREA . . . . . . . . . 5 Location and General Description . . . . . . 5 Site 1 O O O O O O O O O O O O O 0 10 Site 2 O I O O O O O I I O O O O O 10 Site 3 O O O O O O O O O O O O O O 10 Site 4 O O O O O O O O O O 0 0 O O 11 Site 5 O O 0 O O O O O O O 0 O O O 11 Site 6 O O O O O O O O O O O O O I 11 Site 7 O O O O O O O O O O O O O O 11 Site 8 O O O O O O O O O O O O O I 12 METHODS AND MATERIALS . . . . . . . . . . 13 RESULTS I 0 O O O O O O O O O O O O 0 17 Population Density . . . . . . . . . . 20 Numbers of Species . . . . . . . . . . 20 Species Diversity . . . . . . . . . . . 27 Fish Species . . . . . . . . . . . . 34 DISCUSSION . . . . . . . . . . . . . . 38 LITERATURE CITED 0 O C O O O I O O O O O 4 6 APPENDICES Appendix A. Water Quality Parameters . . . . . . . 50 B. Heavy Metal Concentrations . . . . . . 55 iii Appendix C. Species and Total Numbers of Invertebrates Collected . . . . . . . . . . D. Species Diversity . . . . . . . . E. Photographs of Stream Conditions . . . iv Page 57 63 64 LIST OF TABLES Table Page 1. Tukey's multiple range test applied t3 mean numbers of individuals per ft. collected in four collections . . . . . 25 2. Tukey's multiple range test applied to mean numbers of species taken in four collections . . . . . . . . . . . 26 3. Tukey's multiple range test applied to mean species diversity (3), as calculated by Shannon's formula, in four collections . . . . . . . . . . . 28 4. Tukey's multiple range test applied to mean species diversity (d), as calculated by Brillouin's formula, in four collections . . . . . . . . 29 5. Mean annual percent composition of the dominant orders, exclusive of the dipteran family Chironomidae, at the control and Native Creek (sites 6 and 7). . . . . . . . . . . . . 33 6. Species of fish collected from the eight study sites in September, 1971 and June, 1972 . . . . . . . . . 37 Al. Water quality parameters at the eight Mineral River and Native Creek study sites on 7/24/71, in mg/liter where applicable . . . . . . . . . 50 A2. Water quality parameters at the eight Mineral River and Native Creek study sites and at Portal Creek on 9/8/71, in mg/liter where applicable . . . . . Sl Table A3. A4. A5. Bl. B2. C1. C2. C3. C4. Water quality parameters at six of the eight Mineral River and Native Creek study sites and at Portal Creek on 12/29/71, in mg/liter where applicable . . . . . . . . . . Water quality parameters at the eight Mineral River and Native Creek study sites and at Portal Creek on 6/6/72, in mg/liter where applicable . . . . Water quality parameters at the eight Mineral River and Native Creek study sites and at Portal Creek on 9/12/72, in mg/liter where applicable . . . . Concentrations of heavy metals at the eight Mineral River and Native Creek study sites on 7/24/71 in mg/liter . . Concentrations of heavy metals at the eight Mineral River and Native Creek study sites on 9/8/71 in mg/liter . . Species and total numbers of invertebrates collected from the eight study sites on the Mineral River and Native Creek during the period 7/14/71—7/23/71 . . Species and total numbers of invertebrates collected from the eight study sites on the Mineral River and Native Creek during the period 8/13/71-9/3/71 . . Species and total numbers of invertebrates collected from six of the eight study sites on the Mineral River and Native Creek during the period 10/19/71- 10/23/71 . . . . . . . . . . Species and total numbers of invertebrates collected from seven of the eight study sites on the Mineral River and Native Creek during the period 6/7/71- 6/14/71 . . . . . . . . . . . vi Page 52 53 54 55 56 S7 59 61 62 Table Page D1. Species diversity (3), as calculated by Shannon's formula, at the eight study sites from July, 1971 to June, 1972 . . . . . . . . . . . . 63 D2. Species diversity (d), as calculated by Brillouin's formula, at the eight study sites from July, 1971 to June, 1972 . . . . . . . . . . . . 63 vii Figure 1. E1. E2. E3. LIST OF FIGURES Map of the Mineral River and Native Creek showing the location of the study Sites 0 O O O O O O O O O O 0 Density of benthic macroinvertebrates at the eight study sites in July and August, 1971 (Y’i 1 SE) . . . . . . Density of benthic macroinvertebrates at the eight study sites_in October, 1971 and June, 1972 (Y t 1 SE) . . . Species diversity (3), as calculated by Shannon's formula, at the eight study sites from July, 1971 to June, 1972 . . Percent of the total number of individuals which belong to the family Chironomidae at the eight study sites from July, 1971 to June, 1972 . . . . . . . Photograph illustrating natural siltation between site 2 and site 3 on 7/9/71 . . Photograph illustrating low flow condi- tions between site 4 and site 5 on 8/13/71 0 O O I O O O O O O 0 Photograph of shale slab stream bottom between site 4 and site 5 on 8/13/71 . viii Page 22 24, 32 36 65 65 67 INTRODUCTION The community structure of benthic macroinverte- brate populations serves as a valuable index of stream conditions because these organisms show a high degree of habitat preference and have low mobility and thus are directly affected by materials entering the environment. Chemical surveys give an indication of the stream condi- tions only at the time of sampling while benthic macro- invertebrate populations can be indicative of present and past environmental conditions (Wilhm, 1967). Gaufin and Tarzwell (1952) note that these organisms are especially valuable because they can be used to delineate critical conditions of short duration during periods when flows are large, dilution is at a maximum, dissolved oxygen is near saturation, and visual evidence of pollution is at a minimum. In comparing chemical and biolOgical data Butcher (1955) showed that the two differed widely when several types of pollution were involved and concluded that pollution should be defined by biological conditions instead of chemical standards. Benthic invertebrates are, therefore, useful as indicators of both the degree and severity of organic pollution. The effects of pollutants on the benthic macroinvertebrates of a stream are signi- ficant because macroinvertebrates are important in aquatic food chains and play an important role in the natural purification of polluted waters (Wilhm, 1970a). Two concepts, diversity and redundancy, must be considered when evaluating the species diversity of an environment. Diversity is an index of the number of species present per unit area, while redundancy is an ex- pression of the dominance of one or more species and is inversely proportional to the number of species present (Wilhm, 1967). A stable environment of high water quality is characterized by maximum diversity and minimum redundancy. According to Mathis (1968) polluted streams should have less diversity than non-polluted streams since some Species are unable to survive. The remaining species encounter less competition and are able to produce large numbers of individuals if sufficient nutrients are available. Margalef (1961) pointed out that in the event of a sudden increase of nutrients, the different species take full advantage of their reSpective rates of increase.' Because natural waters are relatively free from harmful effluents and provide extremely stable environments the natural communities characteristic of these waters tend toward more complex assemblages of species. Associations or p0pulations of benthic macro- invertebrates provide a more reliable criterion of organic enrichment than the mere occurrence of a given Species (Gaufin and Tarzwell, 1956). This is based on the assump- tion that actions of the biotic environment and coactions between the biotic components result in a characteristic assemblage of organisms. Gaufin and Tarzwell (1952) note that in using associations of aquatic organisms as indi- cators of pollution, the absence or much reduced numbers of formerly present clean-water species in an area may be as important, or more so, as numbers of known pollutional forms. However, the absence of clean-water forms should not always be taken as definite indication of pollution. A knowledge of the life histories of the various groups of aquatic insects is often helpful in interpreting the mean- ing of their distribution. The time of emergence and the time during which they are in the first instars and are very small should always be considered. Analyses based on associations of species, however, usually involve long lists or descriptions of associations which are often cumbersome to use (Wilhm, 1967). Measures which summarize community structure clearly and briefly are much more valuable in evaluating the effects of organic enrichment. Many investigators agree that diversity indices, based on information theory, permit this summarization of large amounts of information about numbers and kinds of organisms (Gaufin and Tarzwell, 1956; Patten, 1962; Wilhm, 1967; Dickman, 1968; Mathis, 1968). These indices do not attempt to explain causal phenomena, but only estimate the amount of information required to define the community structure (Harrel and Dorris, 1968). Wilhm (1966), in discussing the advantages of information theory over methods based on indicator organisms, pointed out that less precise taxonomic distinctions need be made when using information theory. The only data required for community analysis are total number of recognizable taxa in a unit area. The index should, however, be independent of sample size and be associated closely with the wealth of species, since with increasing sample size, the number of individuals increases considerably faster than the number of Species. The present study involves a comparison of species diversity and species abundance of benthic macroinverte- brates in.natural stream water and in stream water receiv- ing the effluents from domestic and industrial sources. The study was conducted on the Mineral River and Native Creek, a tributary of the Mineral River, near the White Pine Copper Mine, White Pine, Michigan. DESCRIPTION OF STUDY AREA The Mineral River (Figure 1) is approximately 18 km long from its headwaters in the Bergland Hills to its mouth where it empties into Lake Superior. The average gradient is 10.4 m/km. The upper reaches of the river are essen- tially representative of a natural system although past logging Operations in this area have had some effect on the river and the water quality. As a result this part of the river reflects primarily the natural conditions of the river. Near the half-way point the river passes through the community of White Pine where it receives approxi- mately 350,000 gallons of secondary effluent per day from the community's trickling filter sewage treatment plant. In addition, housing develOpment projects in the community and runoff from streets, parking lots and other open areas add an undetermined amount of sediment, oil and associated materials to the river. AS the river continues to Lake Superior it is joined by Native Creek approximately 0.4 km from the river's mouth. Native Creek carries the effluents from the c0pper mine's tailing dams and adds the effects Figure 1. Map of the Mineral River and Native Creek showing the location of the study sites. LIKE SUPERIOR 5 l W“ l- 5 7 401 ' fl .5 E\ :‘ ' - I O u '- ' a 5 '5 I i g 4 a" E Talllu .3. v‘ Dans O ‘ . 3 Sewage { ' I Instant ‘ _'_ ' Plant [$33.3 Wilt. rm . 33:5; cunt I!“ 3232' Wilt. Plat 2 km . Figural of the mining Operation to the river. A few hundred meters upstream from its mouth the Mineral River widens and flows through a horseshoe-shaped bend where it drOps much of its sediment load. Therefore, the cumulative effects of all the factors affecting the water quality are observed at the mouth of the river. From its headwaters to the community of White Pine the Mineral River changes progressively from 1.5 to 4.5 m in width with a maximum depth of 0.6 m throughout most of the year. The bottom type changes from coarse gravel in the headwaters to a clay-gravel mixture in the intermediate zone and finally into a mixture of clay, large rock and small Shale slabs 15-25 cm in diameter, near White Pine. A series of active beaver dams is present in the inter- mediate area. Overhanging vegetation is prevalent and the surrounding area is heavily wooded primarily with second and third growth maple and aspen which stabilizes the soil and stream banks. In the area between White Pine and its confluence with Native Creek the river grades from 4.5 to 9.0 m in width with a maximum depth of l m throughout most of the year. The bottom type changes from that described above (near White Pine) to a mixture of clay and larger shale slabs downstream. In the area where the river is joined by Native Creek, the bottom type is composed of clay and coarse gravel overlain by large shale slabs up to l m in diameter. Less overhanging vegetation is present in this area and the effect of that which is present in the wider sections of the stream is somewhat reduced. This area again is heavily wooded primarily with second and third growth maple but the stream banks are not as well stabil- ized as a result of greater variability of flow rate. Native Creek, which begins and parallels the Mineral River from approximately 5 km below White Pine to its confluence with the Mineral River, resembles the cor- responding portion of the Mineral River. Flow rate and corresponding water depth, however, are highly variable as a result of the variable discharge rate from the tailing dams. Drastic physical changes occur in the Mineral River through the last 0.4 km of its length. Immediately after its confluence with Native Creek, the river begins to widen. In the vicinity of the Highway M—64 bridge the river is approximately 24 m wide with a maximum depth of 2.5 m in the main channel throughout most of the year. The bottom is covered by a layer of clay approximately 20 cm thick. Surrounding vegetation is composed of a mixture of maple, aSpen and spruce, and stream bank stabil- ization is reduced. Eight locations along the river system, chosen for their Similarities in physical parameters, were selected 10 for sampling to assess the impact of each major factor exerting a stress on the river. Site 1 is on the Mineral River approximately 1.5 km upstream from where the river passes under Highway M-64 south (upstream) of White Pine. The river is approx- imately 4.5 m wide with an average depth of 0.3 m. The bottom consists predominantly of gravel and large rocks 15-25 cm in diameter, intermixed with a relatively small amount of clay. Overhanging vegetation is very abundant and the stream banks are well stabilized. Site 2 is on the Mineral River between White Pine and the sewage treatment plant, immediately downstream from the point where the river passes under Highway M-64 north of White Pine. The river is approximately 3 m wide with an average depth of 20 cm. The bottom consists largely of clay and rocks 15—25 cm in diameter. Over- hanging vegetation is abundant and the stream banks are only moderately well stabilized throughout the area. Site 3 is on the Mineral River 0.4 km downstream from the sewage treatment plant. The river is approxi- mately 6 m wide with an average depth of 20 cm. The bottom rubble is generally less than 10 cm in diameter and the clay content is at a minimum. Flow rate is in- creased somewhat as a result of the sewage effluent, overhanging vegetation is abundant and the stream banks are well stabilized. 11 Site 4 is on the Mineral River approximately 3 km below the sewage treatment plant, adjacent to the north- west corner of the northern-most tailing dam. The stream is approximately 9 m wide with an average depth of 0.3 m. Clay and gravel overlain by shale slabs up to 0.6 m in diameter make up the bottom. Overhanging vegetation is abundant though the stream banks are not well stabilized. Site 5 is on the Mineral River approximately 0.4 km from Lake Superior, just upstream from where it is joined by Native Creek. The stream is approximately 9 m wide with an average depth of 0.3 m. The bottom consists of clay and gravel overlain by Shale slabs up to l m in diameter. Overhanging vegetation is abundant and the stream banks are well stabilized. Site 6 is on Native Creek 0.4 km downstream from the entrance of the tailing dam effluents. The stream is 4.5 m wide and varies in depth from 0.2 to 0.7 m, de- pending on the rate of discharge from the tailing dams. Clay and gravel overlain by shale slabs up to 0.3 m in diameter make up the bottom. Overhanging vegetation is fairly abundant and the stream banks are quite well stabilized. Except for a buffer zone, however, the area along one side of the stream is Open due to earth-moving operations in this area. Site 7 is on Native Creek 0.4 km upstream from where it joins the Mineral River. The stream is 4.5 m 12 wide and varies in depth from 0.2-0.6 m, depending upon the rate of discharge from the tailing dams. In other respects the Site and surrounding area are similar to those described for site 5. Site 8 is on the Mineral River between the Highway M-64 bridge and the river's mouth. The river is approxi- mately 24 m wide with a maximum depth of 2.5 m in the main channel. A 20-cm layer of clay covers the bottom and overhanging vegetation occurs only intermittently. A narrow margin along the banks of part of the river lacks woody vegetation which subsequently results in reduced stream-bank stabilization. METHODS AND MATERIALS Benthic macroinvertebrates were collected during four periods. Three samples from each of the 8 sites were taken during each collection period according to a stratified random design of sampling. A random transect across the stream was sampled at each site though the Specific areas sampled were chosen to enhance uniformity in bottom type. A benthic riffle sampler described by Coffman, Cummins, and Wuycheck (1971) and an Ekman Dredge were used to sample the 7 upstream riffle sites and the one downstream pool site respectively. Once collected, the samples consisting of bottom rubble and organic debris were taken immediately to the laboratory where the organic matter was separated from the rubble. Upon separation the organic matter was washed in a sieve (No. 60 U.S. standard soil series with openings of 0.25 mm) and pre- served in 25% formalin. The invertebrates were later removed from the organic debris with the aid of a 10x dissecting microscope, transferred to an ethyl alcohol- glycerin solution, and subsequently identified and counted. 13 14 Two related formulas were used to calculate species diversity of benthic macroinvertebrates. One was Brillouin's (1956) formula for information, or diversity per individual: 1 N! d=“(l°92n1 1 ) N 1"2 ' ... ns. where the total number of individuals of all Species in the community (N) and the number of individuals of Species i (ni) are used to measure the diversity (d) of a com- pletely censused collection treated as a pOpulation. Sterling's log approximation for factorials, as suggested by Pielou (1969), was used where N was equal to or greater than 200. Diversity was also determined with Shannon's formula, an approximation of Brillouin's formula, described by Patten (1962): a:- thm =1 ni/N log2 ni/N where the total number of organisms (N), number of indi- viduals per Species (ni), and number of species (3) in the community are estimated from samples and used to estimate diversity (3) of the total pOpulation. The index (3) expresses the relative importance of each Species in the community, and reflects the manner in 15 which individuals are distributed among species (Harrel and Dorris, 1968). The range of d theoretically varies from zero to any positive number. A value of zero is obtained when all individuals belong to the same species. The maximum value of 3 depends on the number of indi- viduals counted and is obtained when all individuals belong to different Species. Wilhm (1970b) demonstrated that a rarely exceeds nine and is generally between three and four in clean—water stream areas and less than one in polluted stream areas. Periodic analysis of the stream water was con- ducted and seasonal fluctuations in the chemical and physical parameters noted. Analyses for heavy metals (mercury, c0pper, zinc, lead, cadmium, silver, chromium, manganese, magnesium, aluminum and iron) as well as alkalinity, dissolved oxygen and B.O.D. were conducted by the White Pine Copper Company. Suspended and dis- solved solids, turbidity, pH, temperature, hardness and chloride analyses were conducted by the author in accordance with standard methods outlined by American Public Health Association (1965). Where several heavy metals were present the additive toxicity of the combination of metals was cal- culated with the formula: Ca Cb Cn fi+f5+ ...fiil 16 where Ca, Cb and Ch are the measured concentrations of the heavy metals in the receiving water, and La, Lb and Ln are the concentrations permissible for each substance individually (National Technical Advisory Committee, 1968). A value greater than 1.0 indicates the toxicity of the combination of metals is greater than the allow- able maximum suggested. RESULTS Chemical and physical parameters were generally within the range of those of natural stream waters and Similar to those present in other rivers in the vicinity (Doonan and Henrickson, 1969; Michigan Water Resources Commission, 1970). Results of chemical and physical analyses appear in Appendix A. A deviation occurred in the area immediately downstream from the copper mine's surface Operations (site 4). In this area, chlorides and hardness Show a substantial increase in concentration. Portal Creek which carries the mine surface drainage and joins the main river in this area appears to be their source. Periodically, Portal Creek also carries rela- tively high concentrations of suspended and dissolved solids resulting primarily from surface runoff during periods of precipitation. Temperature ranges from a minimum of near 0°C during winter to 23°C during summer in the main stream system. This high summer temperature occurs most often in the downstream areas where the shading effect of over- hanging vegetation is somewhat reduced. Though diurnal 17 18 temperature fluctuations were not measured, it is con- ceivable that during periods of extremely low flow and high ambient temperatures, the water temperature could rise higher than the maximum measured. Dissolved oxygen at each station generally ranged from 80% to 100% saturation and was usually greater than 7.0 mg/l. Again, however, diurnal fluctuations were not measured. During periods of low flow and high tempera- tures, early morning minimum concentrations below the sewage treatment plant would undoubtedly be lower. B.O.D. was usually highest below the sewage treat- ment plant. During June, 1972 an increase in B.O.D. was noted in Native Creek. Decomposition of vegetation due to flooding in the tailing dams was most likely responsible for the increase. Sewage treatment plant records indicate a 65% removal of B.O.D. from the final effluent. Heavy metals were present in concentrations naturally occurring in fresh water (Bowen, 1966; Michigan Water Resources Commission, 1972). Results of the heavy metal analyses appear in Appendix B. Among those analyzed, Fe, Al, Cu, Zn, Mn and Mg were found in detectable concen- trations. Iron, Cu and Zn were below the maximum allow- able concentrations suggested by Newton (1971). (Allow- able concentrations of Al, Mn and Mg were not listed.) The additive toxicity of Fe, Cu and Zn, was calculated and 19 their combined concentrations at each site was found to be less toxic than the allowable maximum suggested by the National Technical Advisory Committee (1968). A slight increase in copper concentration below the sewage treat- ment plant may have been the result of discarded chemical materials entering the sewage system from the mining assay laboratory and other mine facilities. The number of individuals, number of species, and the Shannon and Brillouin diversity values among the eight sites were compared with the use of Tukey's multiple range test at the 0.05 level. Where diversity was equal to zero, indicating all individuals belonged to the same species, no significant difference was assumed between zero and the next highest diversity value if the differ- ence between this value and zero was less than the Tukey critical value. This assumption was necessary since a value of zero could not be formally entered into the statistical analysis. Discussion of the number of indi- viduals collected is based on all individuals. The number of species and the Shannon and Brillouin diversity values were tabulated and calculated with the omission of data concerning the dipteran family Chironomidae and the class Oligochaeta. Results indicate that differences among the study sites result from inherent environmental differences 20 among the areas as well as from human perturbation. Diversity was inversely related to the degree of human perturbation present. The greatest numbers of individuals, as demon- strated by Figures 2 and 3, were collected below the sewage treatment plant and at the mouth of the river. Table 1 indicates that no significant difference was found between these two sites in two of the four collec- tions. In the remaining two collections, while they were significantly different, they ranked close together. No Significant difference was identified between the mouth of the river at site 8 and Native Creek. Apparent in- creased productivity in these areas was attributed to nutrients present in the sewage treatment plant effluent and from addition of lime and decomposition of organic matter in the tailing dams. This apparent increase in productivity from the sewage treatment plant was quite evident at site 4 but fairly well dissipated at site 5. The number of individuals collected at Site 5 was low and not significantly different from the densities found at the control Site and the rest of the river system, excluding site 3. The greatest numbers of species, as shown in Table 2, were collected from the control Site, Native Creek and site 5. No significant difference was found among these sites in August and October, 1971. In 21 .Imm a n my Hess .umsmse one sees CH mmuflm xosum Osman mcp um mmumubmuum>cflouoce oanucmn mo mpflmcmo .N musmflm 22 tar—(hm a s o u v n N — h p P L p h. gag £2.23 m musmflm -l~ P tar—(hm a v n p :2 ...: r08.~ I 1'? Sees a 1999 a r 23.3 .. gas— .‘I/S'IVIIGIMONI 23 .Amm H H WV whoa .mcso can anma .umnouoo SH mmufim xpsum unmflo may pm moumnnmuum>cflonome oacucmn mo muflmcoo .m musmflm 24 tar—(hm m c «5— .2...— m ousmam 8:3... I I . I ... I I x I I 1966;" I I x I \ \ I u .83 -886 $86 88.2 :2 .338 1.8.2 zW/S'IVIIOIMONI 25 Table 1. Tukey's multiple range test applied to mean numbers of individuals per ft.2 collected in four collections. Means not underscored by the same line are significantly different (P:0.05). July, 1971 Station 2 7 5 l 8 4 3 6 Mean 9.3 27.0 78.0 99.0 106.7 131.7 292.0 694.3 Multiple Range August, 1971 Station 2 5 6 7 l 4 8 3 Mean 27.0 43.7 72.7 84.0 124.7 177.7 204.0 1022.0 Multiple Range October, 1971 Station 2 5 l 6 8 3 Mean 9.0 70.0 72.3 112.7 385.3 453.3 Multiple Range June, 1972 Station 2 6 5 4 3 1 8 Mean 10.7 16.7 50.0 85.7 119.3 257.7 509.3 Multiple Range 26 Table 2. Tukey's multiple range test applied to mean numbers of species taken in four collections. Means not underscored by the same line are significantly different (pr.05). .— July, 1971 Station 8 2 3 5 7 4 6 1 Mean 2.0 2.3 3.0 5.3 5.7 6.3 10.0 13.3 Multiple Range August, 1971 Station 8 3 2 4 5 6 7 1 Mean 3.3 4.7 5.0 6.3 7.7 9.3 11.0 11.7 Multiple Range October, 1971 Station 8 2 3 5 1 6 Mean 2.7 2.7 3.7 6.7 9.0 11.3 Multiple Range June, 1972 Station 4 2 3 8 6 5 1 Mean 2.0 2.3 2.3 2.7 3.0 4.0 13.3 Multiple Range 27 July, 1971 site 5 contained significantly fewer Species than the control and Native Creek. In June, 1972 the control contained significantly more species than the rest of the river system while no Significant differences was found among the rest of the sites. Numbers of species present in Native Creek and the adjacent section of the Mineral River were not significantly different from each other. Sites 2, 3, 4, 5 and 8, containing the lowest numbers of Species, were not significantly different from each other. A constant stress may therefore be acting upon most of the river system to select against many species. A complete listing of numbers of individuals and species collected during the sampling periods at each study site is provided in Appendix C. The Shannon and Brillouin diversity indices agree strongly although the Shannon values are inherently higher than the Brillouin values (Appendix D). Analyses indicate that diversities at the control, Native Creek, and the section of the Mineral River adjacent to Native Creek are higher than those of the other stations. Tables 3 and 4 Show that these sites were not significantly different from each other in July, August and October, 1971. In June, 1972 no significant difference was found among the diversity values for any of the areas downstream from the control while Species diversity at the control was signi- ficantly higher. 28 Table 3. Tukey's multiple range test applied to mean Species diversity (5), as calculated by Shannon's formula, in four collections. Means not underscored by the same line are Significantly different (P:p.05). July, 1971 Station 8 2 3 Mean 0.00 .50 .82 1.74 1.93 2.90 Multiple -—- Range August, 1971 Station 3 8 2 Mean .52 .67 1.59 Multiple 1.90 1.99 2.37 2.51 Range October, 1971 Station 8 3 2 Mean 0.00 .16 .44 Multiple Range June, 1972 Station 4 8 3 Mean 0.00 .33 .51 Multiple 1.81_ 2.20 2.68 .67 .80 .86 Range 2.97 29 Table 4. Tukey's multiple range test applied to mean Species diversity (d), as calculated by Brillouin's formula, in four collections. Means not underscored by the same line are significantly different (P:p.05). July, 1971 Station 8 2 3 5 6 7 4 1 Mean 0.00 .30 .55 1.06 1.27 1.32 1.46 2.32 Multiple Range August, 1971 Station 8 3 2 4 5 6 7 1 Mean .33 .40 1.26 1.56 1.58 1.90 2.06 2.14 Multiple Range October, 1971 Station 8 3 2 5 1 6 Mean 0.00 .12 .29 1.59 ' 1.79 2.24 Multiple Range June, 1972 Station 4 8 3 2 5 6 1 Mean 0.00 .22 .33 .33 .45 .53 2.51 Multiple Range 30 The lowest diversity consistently occurs at White Pine (site 2), at the sewage treatment plant (Site 3), and near the river's mouth (Site 8). Each area reflects the direct effect of human perturbation. The following factors may be reSponsible for environmental rigor at each site: Municipal surface runoff at site 2; introduced sewage effluent resulting in increased B.O.D. at site 3; and channelization and highway construction at site 8. Figure 4 demonstrates that although conditions in these areas lack stability, they, together with the conditions at the rest of the sites, are quite predictable through- out most of the year. Though diversity indices indicate that no signi- ficant difference exists in the community structure of the upstream control and Native Creek, the insect composition of the two areas is somewhat different (Table 5). The data Show that EphemerOptera were more abundant in the control section while the TrichOptera, Coleoptera and Diptera, exclusive of the Chironomidae, were more preva- lent in Native Creek. Gaufin (1958) classifies benthic macroinvertebrates into three categories: 1) intolerant organisms are those restricted to clean-water zones with dissolved oxygen between 75% and 115% saturation; 2) fac- ultative organisms are those found in both clean-water zones and zones of degradation with dissolved oxygen between 40% and 115% saturation; 3) tolerant organisms 31 .mema .mese on Heme .Sesn gone mmuem segue semen may um .MHSEuOM m.coccm:m we omumaooamo mm .Amv mpflmum>flo mmfiommm .v musmflm 32 v madman tor—(hm PSI. -- - .. - 2e. .2... ..\ . l .I§_...§8 ......... who—£2.93 :2 ...... Io..— rm.— 0 [ON s mu an we w um I. ...... "I (s u A 33 Table 5. Mean annual percent composition of the dominant orders, exclusive of the dipteran family Chironomidae, at the control and Native Creek (Sites 6 and 7). Station EphemerOptera Trichoptera Coleoptera Diptera Cbntrol 18 4 9 11 Native Creek 0 13 18 24 are those most abundant in zones of active decomposition with dissolved oxygen between 1% and 40% saturation. It should be noted that the insect composition of Native Creek consists of a greater percentage of facultative individuals. In the order Trichoptera the genera HydrOpsyche and CheumatOpsyche, which are considered facultative, are the most abundant members of the order in the Native Creek community while other genera (£22227 psyche, Negphylax, Oecetis and Psychomyiid) which are often considered intolerant, are more abundant in the control section. Similar genera of ColeOptera and Diptera, which are predominantly facultative, occur in both areas (Gaufin, 1958; Tennessee Stream Pollution Control Board, 1964; Michigan Water Resource Commission, 1969). Species diversity generally ranges from 1.0 to 3.0 at sites 1, 4, s, 6 and 7. Wilhm (1970b) suggests that diversity values within this range are usually indi- cative of moderate degrees of pollution. However, it must 34 be kept in mind that numbers of species and corresponding densities of the Chironomidae and Oligochaeta were not considered in the diversity determinations. Figure 5 des- cribes the portion of the total number of individuals at each Site which belong to the family Chironomidae. This family makes up a moderate to high percentage of the popu— lation density in all areas except sites 5, 6 and 7. The number of Oligochaeta were of moderate importance at sites 3 and 8 only. With this additional information diversity at sites 3, 4 and 8 would definitely be increased. It is quite possible that diversity, at least at Site 1, would be greater than 3.0 and consequently in the range described by Wilhm (1970b) for clean-water streams. Electrofishing methods were employed to collect fish to determine the species composition at each Site. Most of the species collected throughout the regular sampling areas were members of the Cyprinidae family and of no commercial or sport value. A listing of these species appears in Table 6. These Species are generally found under conditions similar to those afforded by the Mineral River (Starrett, 1950; Hubbs and Lagler, 1958). 35 V .msma .ussn on Huma .hadh Eoum mmuflm wosum Osman can an occasocouflco SHHEmm on» on mconn Scans mamsofi>flocfl mo HOQESS Hmuou on» mo unmoumm .m musmflm 36 m musmwm 20:35 a h a n v m N n p n P P r p n b n \ I, .a ...... o. . a ..o/ I was I . \\\ .116 I \ .. . ...zz. JV .J\. at LV\ ’ ./, ... .. I u , .. . .. \ , /. .. . . z z / .0. .\ too I . . r I . I H I I I . . /.(.\ \ Ica ..... «E ...... p I . .. a. .l . l «node-338 / I \ O .. ......... “had .OnBI" I ‘ II E: ...... .8— NOIIISMloa .llifllfld 37 .H open Scum Emmuummz Ex m.m omuomaaoos x AOMOHH63V Esmuufi> cowomumONAuw x Anson» xoonnv mfiamcHOSOM mScHHO>H6ms x x lseeasuu emauuosv unseen usuuoo x AOOQHSQV muoa muoq x “soccfleoss Hmuucmov SEHH muse: x x x Axomnmaxowum xoounv mcmumcooca nowaso x x x x x x AumeSm muacsv HcomumEEoo mSEoumoumu x Aumcacm coeeoov mauscuoo mflmouuoz x Anocflnm Hamuuommv mascompsc mfimouuoz x x x x Amoco mmocxomanv msasumuum manu20chnm x x x x x x Amomo mmocmcoav mmuomumumo manunowceem x x x x x fiasco xoouov msumHSomEouum mSHAOOEmm m s e m e m m H umeutem .msma .mssn can anma .umnEmummm SH mouflm acsum unmfim map Scum omuomaaoo swam mo mmflommm .m OHQMB DISCUSSION Differences in Species diversity among the eight study areas suggests that environmental conditions fluc- tuate to a considerable degree in the various parts of the river system. It is evident that diversity is inversely related to the degree of human perturbation. However, as demonstrated by species diversity in Native Creek, cultural eutrOphication can be controlled to provide an environment consistent with the requirements of a well diversified in- vertebrate pOpulation. Poulson and Culver (1969) suggested that the theoretical major regulators of species diversity are stability, predictability and rigor of the environment. Environments of high species diversity are characterized by high environmental predictability and low variability. Predictability is quite high throughout the Mineral River from season to season although stability appears low where rigor is high. Precipitation in the Mineral River watershed re- sults in much surface runoff and erosion as a result of loosely held clay soils adjacent to much of the stream. 38 39 Though Specific flow rates were not measured, highly variable water levels were observed and are illustrated in Appendix E. Spring flooding appears to be responsible for the low diversity throughout most of the river in June, 1972. Wilhm and Dorris (1966) observed a similar reduc- tion in the numbers of Species present after heavy rainfall and concluded that the increased flow and scouring effect of dislodged sediments washed many organisms away. Natural siltation consistently occurs during and after periods of precipitation throughout the Spring, summer and autumn months and may be exerting a Significant stress within the Mineral River. Figure 1, Appendix E illustrates the apparent magnitude of siltation in one area of the river. Sites 2, 3, 4, 5 and 8 are most affected by this force while sites 6 and 7 are to a lesser extent. The density of the surrounding vegetation at site 1 stabilizes the soils and prevents most erosion. Gaufin (1958) found that upon settling, fine solids formed a blanket over the stream bottom and over anything else to which they could adhere. The resulting substratum afforded no attachment base for most aquatic invertebrates while its suffocation effect eradicated many organisms previously present. Ellis (1936) stated that silt alters aquatic communities through screening out light, changing heat radiation, and retaining organic materials and other substances which create unfavorable 40 conditions on the stream bottom. Siltation is also re- sponsible for filling in Open Spaces among the rocks and rubble on the stream bottom and reducing the number of available habitats. Poulson and Culver (1969) found that such reductions in Spatial heterogeneity resulted in cor- responding reductions of species diversity. Extremely low and variable water levels in late summer (Figure 2, Appendix E) along with high temperatures may be limiting factors to both invertebrates and fish in the Mineral River and consequently are responsible for low Species diversity levels during succeeding seasons. Burton and Odum (1945) indicated that temperature may be one of the most important factors in limiting the distri— bution of fishes in cool swift streams. Stranding of fish in intermittent ponds is not uncommon during the summer in the Mineral River. Starrett (1951) suggests that this may have adverse effects upon them directly and that reduced space due to low water levels inhibits successful spawning in many fish. The creek chub (nggf tilus atromaculatus) was among the most frequently ob- served Species of fish in the Mineral River. The hardi- ness of this Species in drying pools, as mentioned by Shelford (1937), is the apparent reason for its success. The intolerant mottled sculpin (Cottus bairdi) was present throughout the area from the extreme head- waters to Site 2. The brook trout (Salvelinus fontinalis) 41 was absent from Sites 1 and 2, though present approxi- mately 6.5 km upstream from site 1. Bailey (1952) found that sculpins and brook trout often occurred in the same areas, while Smith (1972) stated that this was not always the case. Some factors within the tolerance limits of sculpins appear limiting to trout. Low invertebrate diversity and absence of brook trout indicate a rigorous and unstable environment at site 2. All parameters demonstrate that site 1 is the most stable, predictable and least rigorous of the areas studied, though brook trout requirements present in the extreme headwaters are absent at site 1 and all areas downstream from this point. Chemical and physical parameters do not support the low species diversity found at site 3. The author feels that further analysis is necessary, particularly in determining the magnitude of diurnal oxygen and temperature fluctuations in this area. During late sum- mer when flow rates are at a minimum and temperatures are high, the effluent from the sewage treatment plant is the primary source of water in the river. Septic or near septic conditions may occur, as Gaufin and Tarzwell (1956) suggest, to provide an environment acceptable to only more tolerant species of invertebrates. Although free residual chlorine concentrations downstream from the sewage treatment plant were not measured, they may have been periodically responsible for some reduction of 42 diversity in this area. Zillich (1972) indicates that free chlorine concentrations greater than 0.05 mg/liter are lethal to many species of fish. Although several Species of fish were found in the area, their mobility may have afforded a means of escape from periodically harsh conditions. The peak density of individuals found at this site in August, 1971 was the result of peak Chironomidae and Oligochaeta pOpulationS (Table 2, Appendix B). To alleviate the harsh conditions in the Mineral River below the sewage treatment plant, the White Pine COpper Company plans to pump the treated secondary ef- fluent from the sewage treatment plant directly into the tailing dams. This would provide a 60 to 80 day retention time of the sewage effluent within the tailing dams and facilitate a type of tertiary treatment of the sewage effluent. Fertilization of the tailing dams resulting from this operation will also aid in tailing dam reclama— tion. Operation of this process will be put into practice in the near future. Site 4 exhibits conditions typical of a recovery zone described by Gaufin and Tarzwell (1956). The pOpu- lation density indicates a reduction in productivity from that present at site 3, while the increased species diversity over that of site 3 is responsive to a more stable and less rigorous environment. The increased 43 levels of chlorides (up to 600 mg/l) in this vicinity appear to have little if any toxic effect on stream organisms. Anderson (1948) reports that concentrations of 3,680 mg/l and 920 mg/l of sodium chloride and calcium chloride respectively, are required for immobilization of Daphnia magna, a fairly susceptible invertebrate. The fathead minnow (Pimephales promelas), which is relatively intolerant to sodium chloride has a 96-hour median toxi- city threshold of 8,700 mg/l (Clemens and Jones, 1954). Site 5 shows a further decrease in productivity from site 4 while species diversity remains similar. The predominantly large shale slab stream bottom is suspected by the author to have reduced the efficiency of the sampling apparatus. A similar conclusion was made concernr ing Site 7 and to a lesser extent Sites 4 and 6. Figure 3, Appendix E illustrates conditions typical of these areas. A greater Species diversity than that indicated may there- fore exist in these areas. Conditions in Native Creek, sites 6 and 7, appear to provide an environment of stability approaching that of the control station. However, conditions in Native Creek may be less predictable and more rigorous than those of the control as the Species composition of Native Creek contains a lower percentage of intolerant and a greater percentage of facultative organisms than the control. The high pOpulation density found in July, 1971 was due 44 to the peak density of Simulium vittatum which composed 70% of the pOpulation. By August, 1971 most of the indi- viduals had matured and emerged and were no longer present in the aquatic environment. Low species diversity at Site 8 is not the result of the effluent discharges from the sewage treatment plant and the tailing dams Since sites 4, 5, 6 and 7 receive these effluents first and maintain greater species diversity than Site 8. Rather, excessive natural silta- tion, resulting in an unstable and uniform substratum, provides a habitat, as Gaufin (1958) suggests, conducive to only a few invertebrate Species adapted to this specific type of environment. Occasionally a few individuals of Species other than those of the family Chironomidae or the class Oligochaeta were collected at this site. These indi- viduals are not members of the community which normally inhabits this area but rather were transported by the current from areas upstream from site 8. Gaufin and Tarzwell (1956) indicate that intolerant species which drift into zones of degradation from nearby tributaries are often able to remain alive for periods sufficient to allow them to emerge as adults. The numbers of such clean-water forms are distinctly limited when compared with the pOpulations of organisms usually found in such areas . 45 Effluent discharges influence the invertebrate communities in the Mineral River and Native Creek to create rigorous environmental conditions. Compared to the control area, the influence of the tailing dams is minimal while that of the sewage treatment plant is of considerable magnitude. As well as these obvious cul- tural discharges, the Mineral River system is influenced by flooding, erosion, and natural siltation, alternating with periods of low water. Such natural forces appear to maintain a constant environmental stress evidenced by diversity levels consistently lower than those of the control. LITERATURE CITED LITERATURE CITED American Public Health Association. 1965. Standard methods for the examination of water and waste water. APHA., AWWA. and WPCF., 12th Ed. Boyd Printing Co., Inc., Albany, N.Y. 769 p. Anderson, B. G. 1948. The apparent thresholds of toxicity to Daphnia magna for chlorides of various metals when added to Lake Erie water. Trans. Amer. Fish. Soc. 78: 96-113. Bailey, J. E. 1952. The life history and ecology of the sculpin, Cottus bairdi unctulatus in south— western Montana. Copeia 4: 243-255. Bowen, H. J. M. 1966. Trace elements in biochemistry. Academic Press, London and New York. 241 p. Brillouin, L. 1956. Science and information theory. Academic Press, New York. 320 p. Burton, G. W., and E. P. Odum. 1945. The distribution of stream fish in the vicinity of Mountain Lake, Virginia. Ecology 26: 182-194. Butcher, R. W. 1955. Relation between the biology and the polluted condition of the Trent. Verhandl. Int. Ver. Limnol. 12: 823-827. Clemens, H. P., and W. H. Jones. 1954. Toxicity of brine water from oil wells. Trans. Amer. Fish. Soc. 84: 97-109. Coffman, W. P., K. W. Cummins, and J. C. Wuycheck. 1971. Energy flow in a woodland stream ecosystem: I. Tissue support trOphic structure of the autumnal community. Arch. Hydrobiol. 68(2): 232-276. 46 47 Dickman, M. 1968. Some indices of diversity. Ecology 49(6): 1191-1193. Doonan, C. J., and G. E. Henrickson. 1969. Groundwater in Ontonagon County, Michigan. State of Michigan Geological Survey, Department of Natural Resources, Lansing. Water Investigation 9. 29 p. Ellis, M. M. 1936. Erosion silt as a factor in aquatic environments. Ecology 17: 29-42. Gaufin, A. R. 1958. The effects of pollution on a mid- western stream. Ohio J. Sci. 58: 197-208. Gaufin, A. R., and C. M. Tarzwell. 1952. Aquatic macro- invertebrates as indicators of stream pollution. Publ. Health Rep. 67: 57-67. Gaufin, A. R., and C. M. Tarzwell. 1956. Aquatic macro- invertebrate communities as indicators of organic pollution in Lytle Creek. Sew. Ind. Wastes 28: 906-924. Harrell, R. C., and T. C. Dorris. 1968. Stream order, morphometry, physiochemical conditions, and community structure of benthic macroinvertebrates in an intermittent stream system. Amer. Midl. Nat. 80: 220-251. Hubbs, C. L., and K. F. Lagler. 1958. Fishes of the Great Lakes region. Cranbrook Inst. Sci., Bloomfield Hills, Mich., Bul. No. 26. 213 p. Margalef, R. 1961. Communication of structure in plank- tonic pOpulationS. Limnol. and Oceanogr. 6: 124-128. Mathis, B. J. 1968. Species diversity of benthic macro- invertebrates in three mountain streams. Trans. Ill. Acad. Sci. 61(2): 171-176. Michigan Water Resources Commission. 1969. Biological monitoring of the Jordan River, vicinity of the Jordan River National Fish Hatchery, Elmira, Michigan, September 23 to October 24, 1969. State of Michigan Bureau of Water Management, Water Resources Commission, Department of Natural Resources, Lansing. 47 p. 48 Michigan Water Resources Commission. 1970. Survey of background water quality in Michigan streams. State of Michigan Bureau of Water Management, Water Resources Commission, Department of Natural Resources, Lansing. 47 p. Michigan Water Resources Commission. 1972. Heavy metals in surface waters, sediments and fish in Michigan. State of Michigan Bureau of Water Management, Water Resources Commission, Department of Natural Resources, Lansing. July. 58 p. National Technical Advisory Committee. 1968. Water quality criteria. Report to the Secretary of the Interior. Federal Water Pollution Control Administration, Washington, D.C. 234 p. Newton, M. E. 1971. Rational used in making recommenda- tions for allowable concentrations of various substances discharged by municipalities and industries throughout Michigan. State of Michigan Bureau of Water Management, Water Resources Commission, Department of Natural Resources, Lansing. July. 7 p. Patten, B. C. 1962. Species diversity in net phyto- plankton of Raritan Bay. J. Mar. Res. 20: 57-75. Pielou, E. C. 1969. An introduction to mathematical ecology. Wiley--Interscience, A division of John Wiley and Sons, New York, London, Sydney, Toronto. 286 p. Poulson, T. L., and D. C. Culver. 1969. Diversity in terrestrial cave communities. Ecology 50: 153-158. Shelford, V. E. 1937. Animal communities in temperate America. Geogr. Soc. Chicago, 2nd Ed., Bul. 5. 368 p. Smith, W. L. 1972. The dynamics of brown trout (Salmo trutta) and sculpin (Cottus EEE') pOpulationS as indicators of eutrOphication. Unpub. Ph.D. thesis, Michigan State University Library. 43 p. Starrett, W. C. 1950. Distribution of the fishes of Boone County, Iowa, with Special reference to the minnows and darters. Amer. Midl. Nat. 43: 112-127. 49 Starrett, W. C. 1951. Some factors affecting the abundance of minnows in the Des Moines River, Iowa. Ecology 32: 13-27. Tennessee Stream Pollution Control Board. 1964. Water quality requirements for Elmid beetles with larval and adult keys to the eastern genera. Tennessee Department of Public Health, Nashville, Tennessee. 14 p. Wilhm, J. L. 1967. Comparison of some diversity indices applied to pOpulationS of benthic macroinverte- brates in a stream receiving organic wastes. J. Water Pol. Contr. Fed. 39: 1673-1683. Wilhm, J. L. 1968. Use of biomass units in Shannon's formula. Ecology 49(1): 153-156. Wilhm, J. L. 1970a. Some aspects of structure and func- tion of benthic macroinvertebrate populations in a spring. Amer. Midl. Nat. 84(1): 20-35. Wilhm, J. L. 1970b. Range of diversity index in benthic macroinvertebrate pOpulations. J. Water Pol. Contr. Fed. 42: R221-R224. Wilhm, J. L., and T. C. Dorris. 1966. Species diversity of benthic macroinvertebrates in a stream re- ceiving domestic and oil refinery effluents. Amer. Midl. Nat. 76: 427-449. Zillich, J. A. 1972. Toxicity of combined chlorine residuals to freshwater fish. J. Water Pol. APPENDICES APPENDIX A WATER QUALITY PARAMETERS 50 xmmuo msnusz. m.~ m.o 0.5 5.0 Asuo-mc .o.o.m mm em mm mm A.umm we .o.o m.m v.m v.5 m.n commxo .mmHo ma AH SH ma mm ms ma ma no.3 .esme omm on mo omv 0mm v H H mooHuoHnu Hmm mm om mmv 004 mm om gm mmmcoumm mvm vmm «Hm mam vmm mom mmm mOH A.mmHQv mUHHom em me 4H mm we a m em A.nnsmv useHom mm mH mH hm Hm mH m Hv muHoHnnoa m.n m.s m.» o.m m.» H.n v.5 4.5 mm m «b so m 6 m m H coHumuucoocoo umumsmumm .OHQMOHHQQM muons umuHH\ms SH .Hn\vm\n co mmuHm mosum xmouo m>Huwz one uo>Hm HmumcHz uano 0:» pm muoumsmumm quHmsv nouns .Ha mHnma 51 e muHm ocm m ouHm comzuoo uo>Hm HmuocHz mcHonuuxmmuo Hmuuomss xwouo O>Hu62s m.m m.m o.om 0.8 Isnoumc .o.o.m mHH mas mm 80H 1.88m so .o.o m.m 0.0H o.m 0.0H sumsxo .nuso -- mm on mm mm mH as mm ma loos .8289 as was 0mm 004 «CH 40H emH 0H N museuoHso we as 48H 55H S5 05 He mHH om unmsentm GMH ems eem omm mHH me eHN mes ONH l.umeov meeeom He m5 N 4H em om NH m e A.eusmv useeom mm mm 4 me we em am we m sueeenuse m.5 m.5 5.5 5.5 5.5 o.m 5.5 m.5 H.5 mu ««m m «5 «O m v m m H umumsmumm coHumuucmocoo .mHQMOHHmmm muons nouHH\mE SH .H5\m\m co xoouo Hmuuom no one mmuHm xosum xmouo m>Humz can um>Hm HMHOSHZ ucmHm ecu um mumumsmumm muHHmsq umumz .m4 mHnms 52 v ouHm pom m muHm cmmSumn Hm>Hm HmumcHz mcHomllxmmuo Hmuuomss xmmuo O>Humz« 0.0 5.0 0.5 0.0 1000-00 .o.o.m m0 00 00 00 1.000 00 .o.0 lsuo0umneeoo.av «.mH 0.0a 0.0H 0.0a 0000xo .uueu 0.H 0.0 0.H 0.0 no.0 .neme 0.500 0.00s 0.0HH 0.0HN 0.0a 0.5 0.0 museuoaso 000 00a 00H 000 00 H0 00 nnuseunm 000 000 0H0 000 sad 00 00 1.00500 mseeom 00H 00 0 00m 5H m 0 A.mmva useHom 000 0.00 0.00 000 0.00 0.HH 0.0H sueeenuse 0.5 0.0 0.0 0.0 0.0 3.5 0.5 me «eh m «o v m N H coHumuucmocoo umuwamumm .OHQSOHHQQM muons nouHH\mE cH .Hn\mN\NH co xmmuo Hmuuom um can mouHm Spoum xomuo O>Humz one um>Hm HmumcHz ucmHm can no me um mumumsmumm muHHmsw Moumz .m< anma 53 w muHm SSS m muHm Somaumn um>Hm HmumSHz mSHonalxmmHU Hmuuomts xmwuo m>Humz« 0.0 0.0H 0.0 0.0 1000-00 .o.o.m 00 000 000 00 1.000 00 .o.n 0.0 0.0 0.0 0.0 sumsxo .0000 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 no.0 .0500 0.000 0.000 0.00 0.00 0.500 0.000 0.000 0.000 0.0 mueHuoHso 00 00 00 00 00 00 00 00 00 suHsHanxas 000 000 00 00 000 000 00 00 00 unmsennm 0.00 0.50 0.00 0.00 0.50 0.00 0.H0 0.0 0.0 HueeHnuse 0.0 0.0 5.0 0.0 0.0 0.0 0.5 0.5 0.5 we 000.0v 000.0v 000.0v 000.0v 000.0v 000.0 000.0v 000.0v 000.0v umeuoo «am 0 «5 «0 m w m N H umumsmumm SoHumuuSOOSOO wooum xomuo m>Humz USS um>Hm HSHOSHS uanm OS» um mnmumsmumm muHHqu noun: .OHSSOHHmmm muons umuHH\mE SH .N5\0\0 So xmmuo Hmuuom um OSm mmuHm .v4 OHQMB 54 .0 muHm USS m mun Sensuon 00>Hm HSHOSHZ mSHonnuxomuu Hmuuomst 0S00 00:0 00 0:000000 Emu mSHHHmu mSH>Hmomu HOS 003 .5 OUHm .xmmuo m>Humz umsoHnuxmmHU m>Humzs 02000.0-2000.00 000 000 55 000 0.000 00 .o.e 05000.0-5000u00 0.00 0.00 0.5 0.00 summxo .0000 1su00.0ueuo0.00 0.00 0.00 0.00 0.00 loos .mgma 05000.0-2000u00 00 000 00 000 00 000 0.000 00 .o.o AS000.0-2000.00 0.00 0.00 0.0 0.00 0.00 0.00 sm0sxo .0000 0E000.0us000.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0o.v .0500 0000 0.000 0.00 0.55 0.500 0.000 00.0 00.0 00.0 0000000so 0000 000 000 000 000 000 00 00 00 000:0000 0000 000 000 000 000 0000 050 000 000 1.00000 000000 00 00 0 00 00 00 00 0 00 1.00000 000000 0.00 0.00 0.50 0.00 0.00 0.00 0.00 0.00 0.00 50000nnse 0.5 5.5 5.5 0.0 0.5 0.5 0.5 0.5 0.0 mm ««m m «5 so m 0 m m H umumsmumm GOHuMHuGOOGOU .mHnmoHHmmm muons umuHH\mE SH .m5\~H\m So xmouo Hmuuom um USS mouHm mosum xmmuo o>Humz 0S6 Hm>Hm HSHOSHE uanm OS» um mumumeumm auHHqu umumz .mm OHQSB APPENDIX B HEAVY METAL CONCENTRATIONS 55 50050 0>0502. 000.0v 000.0v 000.0v 000.05 000.0v 0500502 00.0v 00.0v 00.05 00.0v 00.05 5505000 000.0 000.0 000.0 000.0 000.0 0500 00.00 00.0v 00.05 00.05 00.05 0000 00.0 00.0 00.0 00.5 00.0 500005002 00.0 00.0 00.0 00.0 00.0 000500502 000.00 000.00 000.0v 000.0v 000.0v 500000 00.05 00.00 00.05 00.0v 00.0v 55050550 00.0 00.0v 00.05 00.0 00.0 55505005 Ho.ov Ho.ov Ho.ov Ho.ov 0H.o SouH 00.0v 00.0v 00.0v 00.0v 00.0v 500000 0 .5 .0 0 0 Hmuosmumm SOHumuuSOOSOU m>Humz 0S0 .505HH\mE SH H5\0m\5 So mmuHm 50550 20050 50>Hm H050SH2 uanm OS» 50 mHmums >>00S mo 0SOH5055SmoSoo .Hm OHQMB 56 0 muHm 0S0 m ouHm Smmsumn 50>Hm HmumSHz mSHOnnuxmouo-Hmuuom«« x0050 0>0502. 000.05 000.05 000.05 000.05 000.05 000.05 000.05 000.05 000.05 0500502 00.05 00.05 00.05 00.05 00.05 00.05 00.05 00.05 00.05 5005000 000.0 000.0 000.0 000.0 000.0 000.0 000.0 000.0 000.0 0500 00.05 00.05 00.05 00.05 00.05 00.05 00.05 00.05 00.05 0000 00.0 00.0 00.0 00.0 00.5 00.5 00.5 00.0 00.0 500005002 00.0 00.0 00.0 00.0 00.0 00.0 00.0 00.0 00.0 000500502 000.05 000.05 000.05 000.05 000.05 000.0 000.0 000.05 000.05 505500 00.0 00.0 00.05 00.05 00.0 00.0 00.0 00.0 00.0 50050550 00.0 00.0 00.0 00.0 00.0 00.0 00.0 00.0 00.0 50505005 00.0 00.05 00.05 00.05 00.0 50.0 00.0 00.0 00.0 5050 00.05 00.05 00.05 00.05 00.05 00.05 00.05 00.05 00.05 50>000 ..5 0 .5 .0 0 0 0 0 0 505050505 SoHumuuSSOSOU .50500\05 50 05\0\0 50 00500 00050 x0050 O>Humz 0S0 50>Hm HmumSHz uanm on» 50 mHmums >>00£ mo mSOHumuuSOOSOU .Nm OHQMB APPENDIX C SPECIES AND TOTAL NUMBERS OF INVERTEBRATES COLLECTED 57 Table C1. Species and total numbers of invertebrates collected from the eight study sites on the Mineral River and Native Creek during the period 7/14/71-7/23/71. Species TYPE Number Collected 4 5 6 7 8 OLIGOCHAETA HIRUDINEA Dina g2. EPHEMEROPTERA Ephemera simulans Leptophlebia nebulosa Caenis _p_. Tricorythodes _p: Baetidae MBGALOPTERA Sialis s2: ODONATA Cordulegaster sayi 090009009905 s2: TRICHOPTERA Cheumatopsyche gpp, gydrqpsyche bifida HydrOpsyche slossonae Hydropsyche recurvata Hgdropsyche cuanis EycnOpsyche EB: Neophxlax g2, Oecetis s2, Psychomyiid Genus A COLEOPTERA thioservus gpp, Ordobrevia gpp, Zaitzevia £22: Dubiraphia g2: Deronectes g2: Laccobius _p_. H Hui"! H H H m l-‘ hJO‘k>w NOBU'UI P‘h‘h‘ wafim 21 30 29 32 180 71 13 17 10 58 Table Cl. Continued Number Collected Species TYPE 1 2 3 4 5 6 7 8 DIPTERA Tipula g2, Eriocerus longicornis Tabanus EB: Simulium vittatum Atherix variegata 2 1 Palpggzia gpp: l3 2 26 2 6 4 Empididae 5 151 l 190 23 845 351 131 163 19 288 9 1471 "I'U'U'UHHJ Chironomidae '11 GASTROPODA Phxsa g2: T 1 59 Table C2. Species and total numbers of invertebrates collected from the eight study sites on the Mineral River and Native Creek during the period 8/13/71-9/3/71. Number Collected Species TYPE 1 2 3 4 5 6 7 8 OLIGOCHAETA 9 2 1216 16 ll 19 288 HIRUDINEA Mollibdella grandis l 5 Nephelopsis obscure 1 EPHEMEROPTERA Ephemera simulans I 9 Leptophlebia nebulosa I 27 Caenis s2: 25 Stenonema s2: F 1 MEGALOPTERA Sialis _s_p. F 2 19 4 Nigronia Ep, 1 LEPIDOPTERA Noctuidae 4 ODONATA Cordulegaster saxi 1 gphiogomphus s2, 1 Aeshnidae 3 TRICHOPTERA Cheumatopsyche s22, F 1 4 1 Hydropsyche slossonae I 7 14 11 7 gxdropsyche cuanis I 6 Hydropsyche bifida F 17 55 23 19 ggdropsyche recurvata 2 2 Bycnopsyche _p, I 2 Oecetis g2, I 1 1 1 PhylocentroPis s2: 1 60 Table C2. Continued Number Collected Species TYPE 1 2 3 4 5 6 7 8 COLEOPTERA Optioservus s22, F Ordobrevia spa. Zaitzevia s22, Dubiraphia EB: F 3 Berosus 33. F 4 Carabidae 1 0"me N DIPTERA Eriocera longicornis Antocha saxicola Atherix variegata Tabanus .2' Palpomxia gpp, Empididae Chironomidae 39 5 11 22 6S 5 4 1 5 1 17 8 78 16 4 243 30 1778 476 21 34 54 308 '11'11'11'11'11HH w GASTROPODA ngsa EBB: T 2 3 4 61 Table C3. Species and total numbers of invertebrates collected from six of the eight study sites on the Mineral River and Native Creek during the period 10/19/71-10/23/71. Number Collected Species TYPE 1 2 3 5 6 8 OLIGOCHAETA 9 288 45 157 542 EPHEMEROPTERA Ephemera simulans I 15 LeptOphlebia nebulosa I 19 Caenis pp. F 15 Baetidae F 1 MEGALOPTERA Sialis pp. F l 1 TRICHOPTERA Cheumatopsyche ppp. F 4 8 ggdropsyche slossonae I 20 6 gydropsxche bifida F 38 21 Ochnotrichia riesi 2 1 Oecetis pp. I 4 Psychomyiid Genus A I 1 l COLEOPTERA thioservus pp. F 1 Ordobrevia pp. 1 Zaitzevia ppp. 1 S Dubiraphia pp. F 9 Deronectes pp. 3 Berosus pp. F l DIPTERA Eriocera longicornis I 4 Antocha saxicola I 22 15 Tabanus pp. F 5 Atherix variegata I 15 Pe ri coma _p_. 3 Palpomxia pp. F 16 13 96 24 17 12 Simulium vittatum F 4 Empididae F 9 Chironomidae F 20 12 1174 55 71 572 GASTROPODA Phxsa pp. T 2 15 Helosoma pp. F 2 meaea _p_. 3 FELECYPODA Sphaerium pp. T 9 Table C4. 62 Species and total numbers of invertebrates collected from seven of the eight study sites on the Mineral River and Native Creek during the period 6/7/71-6/14/71. Species TYPE Number Collected 1 2 3 4 5 6 8 OLIGOCHAETA HIRUDINEA Glossiphonia copplanata EPHEMEROPTERA Ephemera simulans Caenis pp, Stenonema ppp, Baetidae PLECOPTERA Acroneuria internata ODONATA Cordulegaster saxi gphiogomphus _p, TRICHOPTERA Hydropsyche bifida Helicopsyche borealis Pycnopsyche ppp, Psychomyiid Genus A COLEOPTERA thioservus pp, Ordobrevia pp, Zaitzevia pp, Dubiraphia.Jg. Derone ctes _p, Berosus _p, Anchodemus ppp, Helodidae DIPTERA Eriocera longicornis Tipula pp, Tabanus pp, Simulium vittatum Chaoborus _p. Palpopxxia ppp. Empididae Chironomidae PELECYPODA Sphaerium _p_. HHH'IJ "J'U'EIH "1'11“! 11 26 33 14 w-bw hUHubw F‘k‘ 22 24 400 22 NH 6 1 28 327 5 14 1 1336 U§ 1 1 8 251 128 36 176 APPENDIX D SPECIES DIVERSITY 00. 00.0 00.0 00.0 00.0 00. 00. 00.0 050050000 005554 5002 00. null. 00. 00. 00.0 00. 00. 00.0 0000 .0500 oo.o IIII v~.~ mm.0 IIII. «0. mm. 00.0 0000 .50nouoo 00. 00.0 00.0 00.0 00.0 00. 00.0 00.0 0000 .500000 00.0 00.0 00.0 00.0 00.0 00. 00. 00.0 0000 .0000 0 0 0 0 0 0 0 0 0500 .0000 .0500 05 0000 .0000 5055 00500 00050 5:000 055 50 .0058000 0.505000005 an 0050050000 00 .000 000000>00 00000mm .mo 0000B 3 6 mm. mo.~ m0.0 mv.0 0m.0 om. om. mm.~ 050000>0n 005555 5002 mm. Illl om. mm. oo.o om. no. 0m.~ ~0m0 .0556 00.0 null 00.0 00.0 1111. 00. 00. 00.0 0000 .5050500 no. 0m.~ v0.~ om.0 00.0 mm. mm.0 0m.~ 0000 .505055 00.0 00.0 00.0 00.0 00.0 00. 00. 00.0 0000 .0000 m 0 m m 0 m N 0 050a .0000 .0500 05 0000 .0000 5050 00500 00050 55m00 055 50 .0058000 0.505505m an 0050050000 00 .va 050mu0>00 m00o0mm .00 00009 APPENDIX E PHOTOGRAPHS OF STREAM CONDITIONS 64 Figure El. Photograph illustrating natural siltation between site 2 and site 3 on 7/9/71. Figure E2. Photograph illustrating low flow conditions between site 4 and site 5 on 8/13/71. 65 Figure E1 Figure E2 66 Figure E3. Photograph of shale slab stream bottom between site 4 and site 5 on 8/13/71. 67 HICHIGQN STQTE UNIV. LIBRQRIES 13293010736654