Dynamics of Chemical and Physical Characteristics of Water, Bottom Muds, and Aquatic Life in a Large Impoundment on a River J. M. Lawrence ZOOLOGY-ENTOMOLOGY DEPARTMENT SERIES FISHERIES NO. 6 AGRICULTURAL EXPERIMENT STATION AUBURN UNIVERSITY E. V. Smith, Director May 1968 Auburn, Alabama f FINAL REPORT ON OWRR PROJECT B-005-ALA DYNAMICS OF CHEMICAL AND PHYSICAL CHARACTERISTICS OF WATER BOTTOM MUDS, AND AQUATIC LIFE IN A LARGE IMPOUNDMENT ON A RIVER J. M. Lawrence Project Leader Matching Grant Agreement No. 14-01-0001-572 Period of Research May, 1965 - December, 1967 The work upon which this report is based was supported in part by funds provided by: Auburn University Agricultural Experiment Station Auburn University Water Resources Research Institute Office of Water Resources Research, USDI, as authorized under the Water Resources Research Act of 1964. March, 1968 REPORT OUTLINE i. INTRODUCTION ................................... .. 2. DESCRIPTION OF LAKE EUFAULA AND ITS DRAINAGE AREA . 3. METHODS OF CHEMICAL AND PHYSICAL ANALYSES OF WATER IND EXTRACTS FROM SUSPENDED MATTER, SOIL, PLANTS, AND FISH ................ 4. SAMPLING EQUIPMENT AND PROCEDURES 5. RESULTS AND DISCUSSION ............................ a. Chemical and Physical Characteristics of Water .......................... b. Chemical Characteristics of Bottom Soils.. c. Chemical Composition of Aquatic Plants.... d. Chemical Composition of Freshwater Fish... 6. SUMMARY......................... APPENDIX TABLES ................................... LITERATURiE CITED ................... Page 3 8 14 44 55 .57 128 143 168 184 197 216 DYNAMICS OF CHEMICAL AND PHYSICAL CHARACTERISTICS OF WATER, BOTTOM MUDS AND AQUATIC LIFE- IN A LARGE IMPOUNDMENT ON A RIVER INTRODUCTION Physical and chemical conditions existing in various river systems and in some impoundments on these rivers in the United States have been investigated periodically during the past 60 years. Generally, these studies have been conducted either to determine the amount of dissolved and suspended materials carried by the rivers, or to evaluate the habitat for propagation of fisheries. In more recent years the greater emphasis of such studies has been concerned with fisheries and public health aspects of these water areas. Present day thinking of multi-uses of these water areas, primarily the impoundments, has created a pressing need for more complete un- derstanding of physical and chemical conditions in all such areas if full utilization and enjoyment of these areas are to be obtained. In particular, here in the Southeastern United States, it is necessary that we understand the impact that these dynamic chemical-physical conditions have upon both the flora and fauna of our mainstream im- poundments. To obtain this understanding,one must have knowledge of the input- output relationships of salts and organic matter brought into the impoundment by creeks, streams, and rivers, their distribution in water, biota, and bottom muds within the impoundment,and the extent of their downstream movement through the tailwater. The salts and organic matter include that leached from the soils of the watershed, 4 from domestic sewage, and from industrial wastes. This type informa- tion is the basis for evaluating the extent of eutrophication in any impoundment, and since complete river system impoundment is a rather recent event,it is imperative that such information be obtained as rapidly as possible. With these problems in mind, the present study on Lake Eufaula a mainstream impoundment on the Chattahoochee River, was begun. This research had as its objectives: 1. Locate the stratification and density currents in various regions of the reservoir during a 3-year period. 2. Determine the distribution of oxygenated waters (i.e. those water regions suitable for occupancy by fish) in various re- gions of the reservoir throughout each year. 3. Obtain information on the concentrations of plant nutrients, including minor elements and toxic cations in waters and bottom muds of tributary streams, various regions of the reservoir,and its tailwaters during various seasons of the year. 4. Determine concentrations of suspended organic, and inorganic materials present at various water depths in various parts of the reservoir and its tailwaters during various seasons of the year. 5. Determine the distribution, chemical composition, and pro- 1 Lake Eufaula is known as Walter F. George Reservoir by U.S. Army, Corps of Engineers, and as Lake Chattahoochee by Georgia residents. duction of plankton in waters at various depths and regions of the reservoir during various seasons of the year. 6. Determine rate of development, distribution,and chemical composition of rooted aquatic plants at each region sampled in this reservoir. 7. Determine the condition of various species of fish in various portions of the reservoir at different seasons of the year. 8. Correlate data obtained in achieving the above objectives by computer data analyses, and develop prediction techniques for use in future monitoring of water, plant, and fish life in the reservoir. In the Project Outline it was pointed out that these objectives would cover a sufficient period of time prior to the initiation of operation of a paper mill on this reservoir to give a basic pattern of preoperational data, and that it should continue for a sufficient period to accumulate data on any changes brought about by the effluent after the mill became operational. Since the mill did not become operational until early 1967, and sinee a Phase II study of the re- servoir has been approved, this aspect of the research will be in- vestigated as a part of that project. Additional data on flow-dispersion patterns within this reser- voir and in the downstream headwaters of Lake Seminole were obtained under a contract with the Federal Water Pollution Control Administra- tion. Pertinent information from this research will be included and discussed under appropriate sections of this report. Comparative data from one headwater impoundment, Bartlett's Perry Reservoir, and from a downstream impoundment, Lake Seminole were obtained at infrequent intervals, but are of sufficient importance to be incorporated into this report. Under the Phase II study plan these areas will be included in a regular sampling schedule. Since the experiences of the Principal Investigator and his consulting collegues have been primarily on smaller impoundments (mainly farm ponds),some dato, techniques, etc. were developed on these smaller bodies of water. Such information has proved invaluable in the establishment of certain chemical and physical parameters as well as providing leads on more complicated systems that appear operative in large as well as in small areas of impounded waters. It should be emphasized that fertilized or fed form ponds offer an excellent opportunity to evaluate a variety of nutrient pollution effects upon the associated biological community. Thus, much more reliable information on the large impoundment was derived in a shorter time and at less expense. Of necessity, this will be a preliminary summary-type report. Several factors dictate that such a report is the most logical way to summarize Phase I of this study. Firstly, since sufficient re- sidue of funds were available to request on additional 6 months of research, much of the worm weather period was devoted to accumulation of additional data. Secondly, a considerable effort was made through- out the study period to modify, develop, or utilize new techniques to more accurately sample or analyze the materials gathered from the reservoir ; thus, a considerable portion of this report will deal with newer techniques. Thirdly, the time-span of completed study 7 (Phase I) has yielded much valuable but varied data that cannot be adequately evaluated until additional data are collected. The Phase II study will provide the time for accumulating those data needed to give a proper perspective for an analyses of these variables and how they may alter the conditions in an aquatic environment. Since this research was concerned with on elaborate and complicated system that involved weather, chemical, and biological interactions, a broader span in time is a vital factor in deriving reliable estimates of parameters under study. Thus the Phase II report will be utilized for summarizing the more complicated systems involved in this study. DESCRIPTION OF LAKE EUFAULA AND ITS DRAINAGE AREA The Chattahoochee River arises in the foothills of North Georgia, The uppermost impoundment on the river near Buford, Georgia forms Lake Sidney Lanier,which has a surface area of 38,000 acres at pool elevation of 1,070 feet. Its shoreline at this level is 540 miles. The drainage area for this impoundment is 1,040 square miles. The following series of impoundments starts at river 166 which is at Columbus, Georgia,and extends upstream to approximately river mile 196 near West Point, Georgia: Surface area, Elevation Drainage area Reservoir name acres feet square miles Langdale 152 547.7 3,600 Riverview 75 530.5 3,600 Bartlett's Ferry 5,850 404.0 4,260 Goat Rock 940 337.0 4,670 Oliver 2,150 337.0 4,670 North Highland 200 266.4 4,670 Two additional small impoundments on the river within the city lirmits of Columbus, Georgia, have a total area of less than 300 acres. The headwater of Lake Eufaula is adjacent to the lower dam on the river at Columbus (Figure 1). Lake Eufaula was created by a 2.5 mile long dam at mi 75 on 9 AT LANTA G E O R I A A L A B A M COLUMBUS EUFAUI YWALTER F. GEORGE LOCK Si DAI COLUMBIA LOCK 86 DAM JIM WOODRUFF LOCK & F L 00 2 R I D A Figure1 Water resources developments on Apalachicola, Chattahoochee, and Flint Rivers (from U.S. Army, Corps of Engineers). Chattahoochee River near Ft. Gaines, Georgia, and is approximately 85 river miles in length; it has a surface area of 45,000 acres at an elevation of 190 feet and has a shoreline of 620 miles. The total drainage area for this impoundment is 7,460 square miles. Normal operation calls for a full pool on April i, and it remains at this level until it is drawndown to an elevation of 185 feet in November. It is maintained at this elevation through following March. The average depth of the area inundated by this impoundment is 20.4 feet, and maximum depth of water adjacent to the dam is about 90 feet. A cross section (Figure 2) of the reservoir appro- ximately 6 miles above the dam shows that the old river channel forms a deep ditch through the impoundment and accounts for the greater depth at the dam. A drawdown of 5 feet exposes approxi- mately 7,200 acres. A unique feature of this mainstream impoundment is its partial separation at river mile 97, approximately 22 miles above the dam, by 2 parallel causeway-type bridges. At this location the reservoir is 1.25 miles in width andt he causeway openings are bridge spans of approximately 800 feet length across the old river channel. To further complicate the situation, the river channel also parallels the upstream face of the causeway (Figure 3). Thus, these bridged spans operate as 70-foot deep sluice ways between the two sectors of the reservoir. The drainage area for Lake Sidney Lanier is located entirely within the Appalachian foothills physiographic area. The portion of LAKE EUFAULA CROSS SECTION - RIVER MILE 81 Figure 2. Typical configuration of bottom in mid and lower portions of Lake Eufaul. Figure 3. Dual bridge complex-between river miles 96 and 98 on Lake Eufaula. 13 drainage area between Lake Sidney Lanier and Columbus, Georgia, is Piedmont Plateau. The drainage area immediately adjacent to Lake Eufaula is primarily Lower Coastal Plains, but a small portion of the drainage area on the western side of the reservoir is Black Belt soil. It is estimated that less than 20 percent of this entire drainage area is cultivated land. Dispersed throughout this drainage area are numerous towns and cities that discharge both domestic and industrial wastes in varying degrees of stabilization into the Chattahoochee river. Thus, by the time the river reaches the upper end of Lake Eufaula, it has received the effluent from over 3/4 million people and their associated industrial wastes. During early stages (1965) of this research project the degree of sewage stabilization changed from none to complete secondary treatment for both Columbus and Phenix City areas. Also, textile mills located in area of West Point, Georgia, improved their waste treatment facilities when a new mill went into operation in early 1967. A new paper mill, Alabama Kraft Company, located on the reservoir at river mile 120, approximately 40 miles above the dam, began operation in January, 1967. This mill had installed an elaborate waste stabilization plant that required several weeks to fill after the plant started operating. An unusual feature of this disposal system is that the opening for release of effluent is 40 feet below lake surface. This waste was released for about 2 weeks in March and the mill discontinued operation because of a strike and remained closed until mid-May. Thus, their effluent release was interrupted for approximately 8 weeks in this late spring period. METHODS OF CHEMICAL AND PHYSICAL ANALYSES OF WATER AND EXTRACTS FROM SUSPENDED MATTER, SOILS, PLANTS, AND FISH The wet chemical analytical procedures employed in the analyses of water are either those proposed by Standard Methods for Examination of Water and Waste Water, APHA, or modifications of these methods employing Hach chemicals and procedures as given in Hach model DR- EL manual, 3rd Edition (Hach Chemical Co., Ames, Iowa). Initially it was proposed that a majority of the chemical analyses of water would be done by wet chemistry. However, as the project became operative,it was discovered that these procedures were too time-consuming as well as being subject to error to yield the volume and type of data needed for this study. Thus, a considerable amount of effort was expended in devising methods and techniques for utilizing recently developed instruments to provide the required data to accomplish the objectives set forth for this project. Some techniques were simple and became operative early in the life of the project, others were more difficult to de- vise and only became operative in 1967. Other techniques are still in the developmental stages and were never operative during this project. In the paragraphs that follow, the techniques used to obtain chemical and physical data on water, plants, fish, and soils from Lake Eufaula will be outlined. Adapted, new or developmental techniques will be discussed for the appropriate chemical or physical deter- mination. Temperature of Water - Measured to nearest 0.lC (with YSI thermis- 15 tor-type thermometer) in-place to depths of 90 feet, or in sample bottle immediately after it came on-board boat. Dissolved Oxygen in Water - Measured to nearest 0.1 ppm 02 (with YSI model 51 oxygen meter employing silver-gold electrode C1 electrolyte - 0.5 mil thick teflon membrane) in place to depths of 90 feet, or in sample bottle immediately after it came on-board boat. The 02 measurements by YSI model 51 oxygen meter were checked periodically by Winkler method of analyses. pH of Water and Soil - Measured to 0.1 pH value with glass electrode, Photovolt, solid state, battery operated meter. Measurements made in sample bottle immediately after it came on-boatd boat. Resistivity of Water and Soil - Measured as ohms per cm 3 with In- dustrial Instruments resistivity meter employing a wheatstone bridge and a platinum coated probe with a factor of 0.1, or with a soil resistivity cup with a factor of 1; Conductivity = 1/resistivity. Turbidity of Water - Determined by refracted light technique, employing either a Hach turbidimeter or a Coleman nepho-colorimeter. Turbidimeter was standardized with a 47-JTU plastic bar. Nephlometer was standardized on distilled water that had been filtered through 0.45 w Millipore filter. Calculations for Total Solids: Mg/1 dry wt. = 1.32 + 1.1084 JTU Mg/1 dry wt. = 1.83 + 0.1534 nephlo value. Light Penetration into Water - Determined at surface and at 2.5- foot intervals of depth to point of extinction with sealed Weston selenium cells coupled to microampere meter. Surface light in- tensity measured simultaneously by Weston model 756 outdoor light meter with quartz-covered light cells. Free Carbon Dioxide in Water - Determined by titration with 0.05 N NaOH to pH 8.3 to an accuracy of 0.001 ml with micrometer pipette (Method 3.3.1, Standard Methods, APHA, 1960). Calculations: mg/l CO 2 = ml NaOH x 0.05N x 44,000 ml sample Sample size of 100 ml - factor = 22 Total Alkalinity of Water - Determined by titration with O.05N HC1 to pH 5.2 to an accuracy of 0.001 ml with micrometer pipette (Method 403, Standard Methods, APHA, 1960). Calculations: Total alkalinity as mg/l CaCO = ml std. acid x 0.05N x 50,000 ml sample Sample size of 100 ml - factor = 25 , Total carbonates = Total alkalinity (mg/1 CaCO3) x 0.6 . Total Calcium + Magnesium Content or Total Hardness of Water - Det- ermined by titration with EDTA (1 ml EDTA = 1 mg CaCO 3 ) using chrome black T as indicator to an accuracy (visually) of 0.01 ml with burette (Method B, Standard Methods, APHA, 1960). Calculations: Mg/1 CaCO 3 = ml EDTA x 1,000 ml sample Sample size of 100 ml - factor = 10 . 17 Calcium Content of Water - Determined by titration with EDTA (1 ml EDTA = 1 mg CaCO ) using murexide as indicator to an accuracy of 0.01 ml using a Photovolt Lumitron colorimeter (Method C, Standard Methods, APHA; 1960). Calculations: mg/l CaCO 3 = ml EDTA x 1,000 ml sample Sample size of 100 ml - factor = 10 mg/l Ca = ml EDTA x 400.4 ml sample Sample size of 100 ml a factor = 4 Nitrogen as NH 1 in Water - Determined by distillation of raw water (treated with m/2 phosphate buffer) and collection of 100 ml of distillate in dilute boric acid. Color of Nesselerized distillate measured by spectrophotometry at 425 mu (Method B, Standard Methods, APHA, 1960). Phosphorus Content of Water - Determined on water by molybdenum blue method - color developed by stannous chloride and measured by spectrophotometry at 690 mp (Method B, Standard Methods, APHA, 1960). Chlorides in Water - Determined by titration with HgNO (0.0141 N) using diphynylcarbazone indicator to a visual accuracy of 0.01 ml (Hach Method). Calculations: Sample size of 100 ml - factor = 5 , CaCO 3 equivalent = ppm chlorides x 1.41 . Sulfates in Water - Determination by barium sulfate turbidimeter method. Turbidity measurement made on nephlometer and compared with known standards (Hach method). Iron Content of Water (Wet)- Determined colorimetrically with 1-10. phenanthroline. Color measured on colorimeter or on spectrophotometer at 500 mu (Hach Method). Silicates in Water - Determined colorimetrically by Hach's amino acid method. Sample treated with ammonium molybdate and oxalic acid and color developed with amino acid (Hach Method). Sodium Content of Water - Determined by flame photometry, using Coleman Model 21 flame photometer and sodium filter. Potassium Content of Water - Determined by flame photometry, using Coleman Model 21 flame photometer and potassium filter. Carbon in the Aquatic Environment - Carbon dioxide comprises 0.04% of normal air and is highly soluble in water. However, the source of CO 2 in water is seldom from the air phase, but results from CO 2 production by both aerobic and anaerobic decomposition of organic matter. The abundance of the carbon atom in nature(mainly organic matter) is due to its valence of 4 and the ability for these atoms to be linked together in a wide variety of ways. Research on this project was concerned with abundance of inorganic carbon compounds (CO2, HCO 3 , and CO 3 ) as well as assimulated carbon in organic matter. Carbon dioxide and alkalinity relationships in natural waters are shown by following equations: 19 CO 2 + H2CO 3 = HCO 3 + H M(HCO 3 ) M+ + 2 HCO 3 3.33 CO + H20 OHCO + OH A change in concentration of any one of these systems will alter the concentration of other ions and result in a change of pH. The relationships of carbon dioxide, alkalinity and pH in a water with 100 mg/l CaCO 3 total alkalinity are illustrated in Figure 4. Carbon also exists in the aquatic environment in at least 3 organic forms - living organisms, organic detritus, and soluble or- ganic carbon. Each of these forms can eventually contribute to the carbon dioxide content of natural waters. Wet chemical methods for determination of C02 and alkalinity of water, by shifting of the pH, are available and widely used. In the case of CO 2 , the standard base used to elevate the pH may be neutralizing other acid radicals in addition to the free CO 2 . Thus, there is an urgent need for a more specific detection method for free CO 2 in water. Alkalinity on the other hand is determined by a depression of the pH with a standard acid. Here again, the acid may be neutralizing weak base or very weak acid radicals in addition to the carbonate and bicarbonate ions. To date, instrumentation adapted to the direct measurement of CO 2 and alkalinity in water is unsatisfactory for routine use. It is possible, however, to check the total C as determined by wet chemistry for free CO 2 and total alkalinity by a special technique utilizing the Beckman carbonaceous analyzer. This technique also Alkolinity in mg/1 CaCO 3 pM7 8 9 10 11 Carbon dioxide, alkalinity, and pH relationships in a solution with total alkalinity of 100 mag/1 CaCO 3 . 20 Figure 4 . 21 permits the estimation of CO 2 by subtracting that portion of carbon- aceous C contributed by total alkalinity from the total amount ex- pelled by the special technique. This procedure is given in the following discussion of this carbonaceous analyzer. The Beckman laboratory model carbonaceous analyzer is essentially an adapted, carbon train-electric furnace apparatus coupled with an infra red (CO 2 specific) analyzer and a recorder. The carrier gas for the system is oxygen, pressure and flow of which can be regulated at all times. The furnace operates at a temperature of 9601C, thus the injected sample of liquid is immediately burned within the Vycor carbon train and the resulting CO 2 is transported to the IR analyzer by the carrier gas. Sample size is usually 20 p1 and sensitivity of detection is less than .5 ppm C. For total carbon determination, the sample of raw water was homogenized with a tissue homogenizer, then 20 pl were withdrawn from well mixed sample and injected into the analyzer. Because of small sample size, particle size within sample must be less than 50 p to pass freely through bore of injection syringe. The analyzer will complete the analysis for C and recover within 2 minutes. The relative quantity of C passing through the detector cell was re- corded on a chart and the concentration was determined from a curve prepared by obtaining recorded values for known concentrations of C. Three separations of the total C in a water sample are possible; i.e. soluble C, carbonaceous C, and volatile C. By applying appropri- ate relationship equations the particulate matter C and the free CO 2 may be calculated. 22 The determination of soluble C was accomplished by filtering the raw water sample through an 8 p Millipore filter and analyzing the filtrate. To eliminate C contamination in the Millipore filter the pad was pre-washed with 10 ml 0.1 N HC1 followed by a rinse of 10 ml of glass distilled water. The amount of C in particulate matter was then determined as follows: Total C ppm - soluble C ppm = Particulate matter C ppm The determination of carbonaceous C was accomplished by addition of sufficient 1 N HC to the raw water sample to reduce the pH to 3.0. This converted all of the bound (CO ) and half-bound (HCO3) CO 2 to free CO 2 . The free CO 2 was then expelled from the water sample by bubbling with N 2 gas for 5 minutes. At the end of this aeration period the sample was analyzed for the remaining total C content. The carbonaceous C content was then determined as follows: Total C ppm - CO -free total C ppm = Carbonaceous C ppm An estimate of C in free CO 2 in original water sample may be obtained by following calculation: Carbonaceous C ppm - Total alkalinity C ppm = Carbon dioxide C ppm Where total alkalinity C ppm = .12 x ppm CaCO 3 (total alkalinity) Thus, the free CO 2 content could be calculated as follows: CO 2 = C ppm x 3.66 = free CO 2 ppm Total Hardness (water) - Hardness of water is a general term that describes the amount of soap required to produce a foam or lather or the amount of scale produced in boilers pipes, or other units where the temperature is elevated materially. 23 Hardness is caused by divalent metallic and alkaline earth elements that are capable of reacting with soap to form precipi- tates, and with anions in water, which react with heat fo form scale. The following are principal cations and associated anions that pro- duce hardness. The hardness the hardness hardness not Cation Anion Ca HCO Mg SQ Sr Cl Fe NO 3 Mn SiO 3 due to.HC03 is termed carbonate or non-permanent while produced by Cl and 504 is termed permanent (i.e. the destroyed by boilin) Conversion factors from divalent ions to hardness as ppm CaCO 3 are given bel1 ow: Ca to CaCO 3 Mg toCaCO 3 Sr to CaCO 3 Fe to CaCO 3 Mn to CaCO 3 Zn to CaCO 3 Al to CaCO 3 It is readily evident that the term "hardness" is related to domestic and industrial uses of water and may-or may not have the same-undesirable effects biological,.y. It was the opinion of in- = ppm =ppm = ppm ppm = ppm =ppm =ppm Ca Mg Sr Fe Mn Zn Al x x C'C x xC xC xC 2,497 4.116 1.142 1,792 1.822 1.531 3.701 vestigators on this project that the determination of abundance of the various divalent cations and their accompanying anions, within the various components of the aquatic environment would be more informative for the purposes of this investigation. However, since a majority of the prior research has relied upon total hardness determinations, this analytical technique was included on this project to determine how this information would compare with cation composi- tion of water. Actually the EDTA total hardness determination used on this project estimated only that part due to Ca and Mg in solution in filtered water. In future research it is anticipated that specific cation concentrations in water will be determined with modern instrumenta- tiontsuch as the atomic absorption spectrophotometer. Data on the divalent elements and associated anions obtained by this research will be given separately, and their overall re- lationship will be considered in the general discussion of results. Elemental Analyzes with an Atomic Absorption Spectrograph - Some of the metallic and alkaline earth elements in water, plants, soil and fish samples were detected and their concentration determined using a Beckman DB-G spectrophotometer equipped with a laminar flow burner and atomic absorption accessory. Since this is a relatively new instrument for determination of elemental content of a solution, a brief outline of the technique used and a typical concentration- response curve for each selected element will be given in this section. Working solutions, containing all ,elements under study and in the relative concentrations anticipated in a given set of samples, were 25 prepared from stock concentrations within a few hours prior to actual analyses. Fresh mixtures were a necessity to minimize the absorption on glass of certain elements such as chrominum and cobalt, within these dilute mixtures. A typical mixture of elements for analyses of Chattahoochee river water was as follows: Ca 10 ppm Na 5 K 2 Fe 2 Mg 2 Mn 1 Cu 1 Zn 1 Sr 1 A typical mixture of elements used for analyses of diluted ex- tracts of soil, plant, and fish samples was as follows: Ca 25 ppm Na 10 Mg 10 Mn 5 Fe 5 K 5 Sr 2 Zn 2 Cu 1 Pb 1 26 Cr 1 ppm Ni I Co 1 Cd 1 Mo 1 The data obtained on Mg, Zn, Cu, and Fe in 1965 were determined by a Perkin-Elmer Model 303 atomic absorption spectrophotometer,which could be used to analyze only filtered water samples.Data obtained on these and other elements in 1966 and 1967 were determined on a Beckman Atomic Absorption Spectrophotometer equipped with a laminar flow burner that was capable of analyzing raw water samples. Beckman provides two interchangable laminar flow burners for their atomic absorption spectrophotometer, an air-acetylene model and a nitrous oxide-acetylene model. The air-acetylene model is more economical on air and fuel consumption and is a good burner for the type analyses discussed in this report. The nitrous oxide-acetylene burner is a much hotter flame source and is used for detection of such elements as Al and Si. This latter burner model may be operated on air-acetylene and gives very satisfactory results, but the air consumption is 3 to 4 times greater than with the regular air-acetylene burner. This nitrous oxide-acetylene burner also has another fault that causes it to have a "memory" when operated in the cold mode. This contamination arises in the fore end of sprayer chamber which is completely sealed around the sample injector. This sealed space acts as a condensation cell for spray vapors and when a sufficient quantity accumulates it drains into the condenser and some of the 27 vapors are swept along in the air stream to the burner head. This condensation may be corrected in air-acetylene operation by removing the rubber seal from around injector. The laminar flow burner is designed to operate in either the cold or hot mode. In the cold mode the injected sample is transported to the burner as a cold spray mist, and the sensitivity of the AA unit is similar to a regular turbulent flow burner such as employed on P-E 303. When operating in the hot mode the injected sample is pre-heated in the spray chamber and transported through the condenser into the burner head as an aerosol mist. This technique increases the sensitivity of an AA unit approximately 10 times. The principal of atomic absorption spectrophotometry is to pro- vide an energy source that is specific for a given element in its most active ground state, and when a sample of that element is excited within a flame operating between the source and detector it absorbs energy from this source in proportion to its concentration. Thus when this source is operative on an AA unit the scale deflection is set to 100% transmittance. When a sample containing this element is introduced into the flame,its absorption results in a decrease in deflection of the needle toward 0%T in proportion to its concentra- tion. The relative detection ability of an atomic absorption spectro- photometer depends in a large measure upon the output of the hollow cathode source lamp. The amount of energy reaching the photo detection unit can be increased either by a higher micro-ampere input into lamp (which shortens the life of filament) or by increasing the slit 28 width (which reduces the sensitivity of certain wave bands and gives more flame noise on the recorder) or by increasing the gain amplifier (which also results in excessive recorder noise). One way to over- come this low energy difficulty is to operate the AA unit on a half- scale deflection and 2X scale-expand the recorder. To utilize this procedure necessitates dilution of samples to the appropriate con- centration ihat will allow full detection on a half-scale range. It might be pointed out that on full scale deflection reliable results are obtained between 100 and 15% T, and on half-scale de- flection between 50 and 15% T. The individual concentration curves for each element serve as a guide for establishing the optimum op- erational range for most reliable detecion with an AA unit. The major source of error with the Beckman atomic absorption spectrophotometer arose from contamination in the laminar flow burner. When analyzing plant, fish, and soil extracts there was a rather heavy deposit of metallic compounds within the heated sprayer chamber and in the condenser. The only satisfactory method for con- trblling this deposit accumulating and producing an instrument "memory" was to regularly flush the sprayer chamber with 70% ethanol, followed by scrubbing with a bottle brush and again flushing with ethanol and water. When sufficient deposits accumulated the condenser had to be dismantled and the interior flushed with ethanol, scrapped and scrubbed until pactically no reslidue could be removed. While the burner unit was dismantled the fuel injector was removed and thoroughly cleaned. To reduce clogging of tiny holes 29 in injector used on air-acetylene laminar flow burner., a micro-nite filter was installed on the acetylene hose at its junction with the tank pre ssure .regulator. 30 Calcium - at. wt. 40.08. Standard prepared by dissolving 2.4973 g calcium carbonate (Iceland spar) in 10 ml concentrated HC1 and then diluting to 1 liter with glass distilled water. Solution contains 1 mg Ca/ml. Working standards contained from .001 mg Ca/ml to .025 mg Ca/ml. Instrument settings were as follows: Hollow cathode source Ca; Ca-Mg-Al; Ba-Ca-Sr-Mg lamp Wave length 432 mp Slit width .2 mm Current 10 ma Fuel- acetylene 4 psi Air 17 psi Burner flame height .3 in With laminar flow burner operated in hot mode, the sensitivity was 0.01 ppm Ca with standard solution. However, with river or pond waters,the detection was poor, being in the range of 10 to 15 percent of the concentration indicated by EDTA titration. An addition of 0.1 ml of 5% LaO 2 to 10 ml of natural water increased the detection by AA to approximately the same amount indicated by EDTA titration. lX cold lX hot 40 60 100 ? 0 5 10 15 20 25 ppm Typical Ca concentration - response curve. 31 Magnesium - at. wt. 24.32. Standard prepared by dissolving 1.000 g magnesium metal in 10 ml concentrated HC1 and diluting to 1 liter with glass distilled water. Solution contained 1 mg Mg/ml. Working solutions contained from .0001 mg Mg/ml to .005 mg Mg/ml. Instrument settings were as follows: Hollow cathode source Mg; Mg-Ca-Al; Mg-Ca-Sr-Ba lamp Wave length 285 mp Slit width .2 mm Current 10 ma Fuel - acetylene 4 psi Air 17 psi Burner flame height .3 in With laminar flow burner operated in cold mode, the sensitivity was 0.01 ppm Mg with standard solution. With untreated river or lake water,the sensitivity was approximately 90 percent of that obtained when 0.1 ml of 5% LaO 2 was added to 10 ml sample. iX 20.0 40] 7 60, 01 801_ 100 0 1 2 3 4 5 ppm Typical Mg concentration - response curve for cold mode operation. 32 Strontium - at. wt. 87.63. Standard prepared by dissolving 1.6848 g Sr No 3 in glass distilled water and diluting to 1 liter. Solution contains 1 mg St/ml. Working solutions contained from .0002 mg Sr/ml to .002 mg Sr/ml. Instrument settings were as follows: Hollow cathode source Sr; Sr-Ca-Ba-Mg lamp Wave length 460.8 mp Slit width 0.25 mm Current 15 ma Fuel - acetylene 4 psi Air 17 psi Burner heigth .3 in With laminar flow burner operated in hot mode,the sensitivity was .01 ppm Sr with standard solution. With lake and river water,the sensitivity was equally good. 0 20 40 2X 60 80 100 0 1 2 ppm Typical Sr concentration- response curve for hot mode operation. 33 Sodium - at. wt. 22.99. Standard prepared by dissolving 2.5425 g of sodium chloride in 1 liter of glass distilled water. Solution contains 1 mg Na/ml. Working solutions contained from .0001 mg Na/ml to .025 mg Na/ml. Instrument settings were as follows: Hollow cathode source None (Mirror) Wave length 589 mp Slit width .2 mm Current Mirror Fuel - acetylene 4 psi Air 17 psi Burner flame height .3 in Emission type determination using either cold or hot mode of laminar flow burner. Sensitivity<0.01 ppm using either mode. 20 iX 40 60 %T 80 100 0 5 10 ppm Typical Na concentration - response curve for cold mode operation. 34 Iron - at. wt. 55.84. Standard prepared by dissolving 1.000 g iron wire in 20 ml HC1 and then diluting to 1 liter with glass dis- tilled water. Solution contains 1 mg Fe/ml. Working solutions con- tained from .0001 mg Fe/ml to .005 mg Fe/ml. Instrument settings were as follows: Hollow cathode source Fe; Fe-Cu-Mn; Fe-Zn-Mn-Ni lamp Wave length 248 mp Slit width .20 mm Current 20 ma Fuel - acetylene 4 psi Air 17 psi Burner height .3 in With laminar flow burner operated in hot mode the sensitivity was 0.01 ppm Fe with standard solution. With river and lake waters,the sensitivity was equally good. 20 1 40 60 80 2X , / 100 0 1 2 ppm Typical Fe concentration - response curve for hot mode operation. 35 Manganese - at. wt. 54.93. Standard prepared by dissolving 1.000 g manganese metal in 10 m of HC1 and then diluting to 1 liter with glass distilled water. Solution contained 1 mg Mn/ml. Working standards contained from .0001 mg Mn/ml to .002 mg Mn/ml. Instrument settings were as follows: Hollow cathode source Mn; Mn-Fe-Cu; Mn-Fe-Cr-Ni lamp Wave length 279 mp Slit width 0.15 mm Current 15 ma Fuel - acetylene 4 psi Air 17 psi Burner height .3 in With laminar flow burner operated in hot mode,the sensitivity was 1 ppb Mn with standard solution. With pond and river water,the sensitivity was equally good. 20 2X 40 60 80 100 0 1 2 3 4 5 ppm Typical Mn concentration - response curve for hot mode operation. 36 Zinc - at. wt. 65.37. Standard prepared by dissolving 1.000 g zinc metal in 10 ml HC1 and then diluting to 1 liter with glass distilled water. Solution contains 1 mg Zn/ml. Working solutions contained from .0001 mg Zn/ml to .002 mg Zn/ml. Instrument settings were as follows: Hollow cathode source Zn; Zn-Cu-Pb-Sn lamp Wave length 214 mp Slit width .5 mm Current 10 ma Fuel - acetylene 4 psi Air 17 psi Burner flame height .3 in With laminar flow burner operated in hot mode the sensitivity was 1 ppb Zn with standard solution. With lake or river waters,the sensitivity was equally good. 20 1x 40 60 80 - 0 2F ppm Typical Zn concentration - response curve for hot mode operation. 37 Copper - at. wt. 63.57. Standard prepared by dissolving 1.000 g copper foil in 10 ml HNO 3 and then diluting to 1 liter with glass distilled water. Solution contains 1 mg Cu/ml. Working solutions contained from .0001 mg Cu/ml to .002 mg Cu/ml. Instrument settings were as follows: Hollow cathode source Cu; Cu-Fe-Mn; Cu-Zn-Pb-Sn lamp Wave length 324.7 mp Slit width .2 mm Current 10 ma Fuel - acetylene 4 psi Air 17 psi Burner height .3 in. With laminar flow burner operated in hot mode,the sensitivity was 10 ppb Cu with standard solution. With river and lake water, the sensitivity appeared to be about 0.1 ppm Cu. 20 I 40 2X 60 0 1 2 ppm Typical Cu concentration - response curve for hot mode operation. 38 Cadmium - at. wt. 228.8. Standard prepared by dissolving 1.0 g cadmium metal in 10 ml HNO 3 and diluting to 1 liter with glass dis- tilled water. Solution contained 1 mg Cd/ml. Working solutions con- tained from .0001 mg Cd/ml to .002 mg Cd/ml. Instrument settings were as follows: Hollow cathode source Cd lamp Wave length 229 mp Slit width .2 mm Current 8 ma Fuel - acetylene 4 psi Air 17 psi Burner flame h eight .3 in With laminar flow burner operated in hot mode, the sensitivity was 1 ppb Cd with standard solution. 2X 20 40 60 80 100 0 .5 1 ppm Typical Cd concentration - response curve for hot mode operation. 39 Molybdonum - at. wt. 95.95. Standard prepared by dissolving 1 g molybdomum metal in 10 ml HNO 3 and then diluting to 1 liter with glass distilled water. Solution contains 1 mg Mo/ml. Working solutions contained from .0001 mg Mo/ml to .002 mg Mo/ml. Instrument settings were as follows: Hollow cathode source Mo lamp Wave length 313.0 mp Slit width .2 mm Current 15 ma Fuel - acetylene 4-4.4 psi Air 17 psi Burner flame height 0.3 in With laminar flow burner operated in hot mode,the sensitivity was .05 ppm Mo with standard solution. With river and lake water,sensitivity appeared equally good. 20 40 60. 0 1 2 ppm Typical Mo concentration - response curve for hot mode operation. 40 Lead - at. wt. 207.21. Standard prepared by dissolving 1.000 g lead metal in 10 ml HNO 3 and diluting to 1 liter with glass distilled water. Solution contains 1 mg Pb/ml. Working solution contained from .0001 mg Pb/ml to .002 Pb/ml. Instrument settings were as follows: Hollow cathode source Pb; Pb-Cu-Zn-Sn lamp Wave length 283 mp Slit width .2 mm Current 15 Ma Fuel - acetylene 4 psi Air 17 psi Burner flame height .3 in. With laminar flow burner operated in hot mode,the sensitivity was .05 ppm Pb with standard solution. 20 40 60 80 100 Typical Pb concentration - response curve for hot mode operation. 41 Chromium - at. wt. 52.01. Standard prepared by dissolving 1.000 g chromium metal in 10 ml HNO 3 and diluting to 1 liter with glass distilled water. Solution contained 1 mg Cr/ml. Working solutions contained from .0001 mg Cr/ml to .002 mg Cr/ml. Instrument settings were aus follows: Hollow cathode source Cr; Fr-Fe-Mn-Zn lamp Wave length 358 mp Slit width .2 mm Current 12 ma Fuel - acetylene 4 psi Air 17 psi Burner flame height .3 in With laminar flow burner operated in hot mode the sensitivity was .01 ppm Cr with standard solution. 20 404 60. %T 5X 80J 100 0 1 ppm Typical Cr concentration- response curve for hot mode operation. 42 Cobalt - at. wt. 58.93. Standard prepared by dissolving 4.938 g of cobalt nitrate in 1 liter of glass distilled water. Solution contains 1 mg Co/ml. Working solutions contain from .0002 mg Co/ml to .002 mg/Co/ml. Instrument settings were as follows: Hollow cathode source Co lamp Wave length 241 mp Slit width .2 mm Current 15 ma Fuel- acetylene 4 psi Air 17 psi Burner flame height .3 in With laminar flow burner operated in hot mode the sensitivity was .01 ppm Co with standard solution. 20. 5X 40 60I 80 100 0 1 ppm Typical Co concentration - response curve for hot mode operation. 43 Nickel - at. wt. 58.69. Standard prepared by dissolving 1.0 g of nickel metal in 10 ml HNO 3 and diluting to 1 liter with glass dis- tilled water. Solution contained 1 mg Ni/ml. Working solutions contained from .0001 mg Ni/ml to .002 mg Ni/ml. Instrument settings were as follows: Hollow cathode source Ni; Ni-As; Ni-Fe-Cu-Zn lamp Wave length 232 mp Slit width .2 mm Current 15 ma Fuel - acetylene 4 psi Air 17 psi Burner flame height .3 in With laminar flow burner operated in hot modethe sensitivity was .01 ppm Ni with standard solution. 20 40 5X 60 0 1 ppm Typical Ni concentration - response curve for hot mode operation. 44 SAMPLING EQUIPMENT AND PROCEDURES A study of chemical and physical factors in any aquatic en- vironment is no better than the sampling techniques used to obtain the data. As a first requirement, the procedure employed must obtain an adequate and representative sample of the particular factor un- der investigation. Secondly, the procedure must be reproducible by the developing investigator as well as by other investigators. Thirdly, the technique should be as simple to perform and as adaptable to all situations as possible. Lastly, the technique should be as portable and economical as possible. Considerable effort was expended on this study to select or devise techniques which fulfilled the above requirements. Those techniques employed for routine sampling are discussed in this section. Since this study was concerned with sampling a reservoir and tailwater that was over 100 river miles in length it was necessary that all boat equipment be mobile overland as well as on water. Thus, the boat equipment had to be portable on a trailer. Another considera- tion on the size of boat was determined by the character of the wave action on the reservoir. The lower region of this reservoir is notorious for suddenly becoming rough almost daily throughout the summer. Therefore, a 20-foot fiberglass surf-fishing boat, equipped with twin outboard motors, was selected as the principal work boat for this study. Two additional boats and outboard motors utilized for aquatic weed contol research, were also used on this study. All equipment was portable by trailer, and all boats and vehicles were equipped 45 with 2-way radios so that boats and vehicles could be dispatched and coordinated to most efficiently accomplish the particular study underway. Two of the boats were equipped with depth indicators,which saved considerable time in locating old stream and creek channels for water and soil sampling, as well as providing needed information for navigating over various portions of the reservoir. These sounders were also helpful in locating areas of suitable depth for the es- tablishment of aquatic vegetation and for determining the type (sand or muck, clear or stumpy) of reservoir bottom. The recording sounder was used to map cross section profiles of the reservoir bottom. The larger fiberglass boat was equipped with two 12-volt electric hoists including davits. The smaller fiberglass boat was also equipped with a similar type removeable hoist and davit. This equipment proved indespensible in the collection of water and soil samples throughout the entire study. Two of the boats were equipped with voltage convertors, which permitted the use of 110-volt instruments on-board these boats. In addition, a small 1500 watt 110-volt a.c. and 12 volt d.c. alternator was also employed on long runs to provide additional currents for instruments, small motors, and to recharge batteries. Specific instruments utilized in the field included Yellow Springs Instruments model 51 oxygen-temperature meters. In addition to the regular 10-foot lead on standard probes, one probe with an 100-foot lead was available on the large boat. This permitted in-place measurements of temperature and dissolved oxygen concentrations to 46 water depths of 90 feet. A Troxler Electronic Laboratories transistorized portable Scaler model 200 B, equipped with a Troxler pulse height analyzer, model E-200, and a Troxler Model 300 scintillation probe was used on- board boats to determine gamma radiation counts on collected water and soil samples. An Industrial Instruments resistivity meter equipped with a regular platinum probe for measurements in water and a resistivity cup for measurements on soils was avaiable for use on the large boats. A Weston Instruments model 756 daylight type light meter was on-board the boat to measure surface sunlight intensity, and a Weston microampere meter coupled to a triple-selenium-cell submersible light head was utilized to measure light intensity at different water depths. The sensitivity of cells in submersible head was sufficient to require a 1-ohm shunt when the unit was operative in the atmosphere. A Photovolt portable pH - my meter equipped with a glass electrode probe and a platinum electrode probe for measuring pH and redox potential in water and soil samples was also on-board the boats. An American Instruments Company micro photofluorometer equipped to be operated as a portable unit was employed on the larger boat to detect fluorescent type dyes in flow-dispersion studies. Sample collecting equipment regularly employed included 2 -liter capacity Hydro Products deep well water samplers. Since these bottles operated on a single rope, they were attached to the electric hoists on-board the boats at a great savings in time. A Hydro Products Phleger core-type soil sampler with removable 47 plastic-tube liners was employed primarily to collect samples of exposed bottom soils during drawdown periods. An all-plastic sampler was developed by the principal investiga- tor that was capable of collecting surface residue to a depth of 1/4 inch over approximately 0.5 square feet of lake bottom. The sample- collecting chamber was cocked on-board the boat, the sampler lowered to the bottom on a rope, and the collecting chamber activated by a messenger dropped along the rope. The sampler was then retrieved by the rope and the contents of the collecting chamber removed into a plastic pan or bag. Leakage of collected muck was nil as long as the sampler was underwater. A Hach Chemical Company turbidity meter was operated on-board the large boat to determine the amount of suspended matter in water samples. Procedure for Collection of Water Samples Water samples for chemical and plankton analyses were collected with a Hydro Products deep well sampler at the surface and at intervals of 10 or 20 feet of depth - the interval and number of samples collec- ted depending upon the location in the reservoir. As soon as the collected sample came on-board the boat, the top of sample bottle was opened, the oxygen-temperature probe was inserted, and these two parameters measured by the YSI meter. The resistivity and pH of the water sample were also measured by inserting these probes into the water bottle. The turbidity was also determined on each water sample on-board boat by Hach turbidometer. Water for chemical and plankton analyses was withdrawn from sample bottle with a siphon into a 1- quart nalgene plastic bottle that was filled to overflowing and then tightly capped. The sample was then stored in the shade on-board the boat. Chemical and plankton analyses were performed within 24 hours after samples were collected. 49 Procedure for Collecting and Extracting Plankton And Other Suspended Matter Samples (This Technique was Developed in 1967) A portion (usually 200 ml) of each water sample collected for chemical analyses was vacuum filtered and the suspended matter collec- ted on an 8 u pore-size Millipore filter. The filter and its residue was placed in a 50 ml beaker and the residue removed by extracting with 4 ml of hot aqua regia. The extracted filter was washed with distilled water and removed from the beaker. The solution in the beaker was evaporated to dryness. The dried residue was then dissolved in 20 ml of hot 0.1 N HCl and stored in plastic beaker for analyses on atomic absorption spectrophotometer. The filtrate was saved for determinations of its soluble element composition. Procedure for Preserving, Cj1lecting, and Extracting Soil asples Two techniques of soil sampling were employed in this study. Profile soil samples were collected with a Hydro Products Phleger core sampler in shallow water and dewatered areas of the reservoir at various times of the year. In a majority of cases, the cutting tip was forced into the soil for a sufficient depth to collect a 4-to 6- inch profile in the plastic interliner of the sampler. The interliner was removed from the sampler with the soil sample intact and the ends of the liner were closed by stoppers. The liner was brought into the laboratory and the sample of soil was air dried, then separated into a top, and remaining lower portion, ground in a mortar to pass a 40-mesh screen, and stored for analyses. Samples of the interface area adjacent to water and bottom mud were collected throughout the summer of 1967 by the all-plastic hydrosol sampler described earlier. An area of 0.5 or 1 square foot was included in each sample. Immediately after a sample came on- board, the pH, resistivity, gamma count, and redox potential were determined. The entire content of sampler was placed in a one-gallon plastic bottle and transported to the laboratory. The entire content was dried over infrared lamps, weighed, and ground to pass a 40- mesh screen. This dried sample was weighed and stored for analyses. The cation-exchange procedure (Jackson, 1964) was utilized for extracting soil samples. Briefly the procedure was as follows: A 5.0 or 10.0 g sample of dried soil was placed into a 125 ml Erlemmeyer flask and 20 ml NH 4 0 AC was added. Flask was stoppered and 51 then agitated on a mechanical shaker for 15 minutes after which the solution and soil was allowed to stand and react for 24 hours. The soil solution was vacuum filtered through No. 42 filter paper on a Buchner funnel and the soil residue washed with additional 100 ml NH 4 OAC. The filtrate was dried on water bath, and the dried residue was treated with 2 ml H202 + 4 ml 3 N HNO 3 . Flask was covered with watch glass and allowed to stand 30 minutes after which sample was again dried on water bath. The resulting residue was dissolved in 5 ml 6N HCl and diluted to 100 ml with distilled water. This solution was filtered and the filtrate stored in plastic cups for phosphorus and cation analyses. Jackson, M. L. Soil Chemical Analys s. Prentice-Holl, Inc., 498 pp. 1964. 52 Procedure for Collecting and Storing Plant Samples Samples of selected species of rooted aquatic plants were collected at various times and places throughout study period. The intact plant sample was picked up with a digging fork, the soil rinsed from the roots and stems and the intact plant was placed in a plastic bag and stored in the shade. When the sample reached the laboratory the entire plant was washed with tap water to remove all soil and organic debris. The washed sample was then frozen until it could be placed on a freeze-drier. The dried sample was stored in a dessicator until it could be ground in a Wiley mill to pass a 40-mesh screen. The ground, dried sample was then stored in a plastic container for analyses. (1) 'Complete details of this procedure were given in the following thesis: Denton, Jerry B. Relationships between the chemical composition of aquatic plants and water quality. M.S. Thesis, Auburn University, 78 pp. 1966. 53 Procedures for Collecting and Storing Fish Samples(1) Samples of selected species of fish were collected by various techniques at different times and places. Briefly the methods of collecting fish included seining, electric shocking, rotenoning, and dynamiting. Immediately following the picking up of the samples of live fish, they were placed in ice and kept there until they were brought into the laboratory where they were separated by species, and their individual total length, total depth, and weight was determined prior to the fish being frozen. The frozen fish were then dried on a freeze-drier and stored in dessicators until each sample reached a constant dry weight. The dried fish were ground in a Wiley mill to pass a 40-mesh screen. Each ground, dried fish sample was stored in a plastic container for analyses. (I) Complete details on collection procedures, etc. will be found in thesis (now in preparation) of Beverly Clement and Roland Reagan. 54 Methods of Analyses of Plant ( 1 ) and Fish Tissue A 0.5-g sample of dried, ground tissue was incinerated at appro- ximately 500*C for 24 hours. After the ash weight was determined, the ash was dissolved in the crucible with 4 ml of aqua regia. This solution was boiled to dryness and the residue was taken up in 50 ml 0.1N hot HC1. This solution was used for phosphorus and atomic absorption analyses. Total nitrogen content of each dried tissue sample was determined by Coleman Model 29 Nitrogen Analyzer II. Total carbon content of dried tissue sample was determined by Coleman Carbon-Hydrogen Analyser. (1) A different procedure for preparation of plant samples for analyses is described in following thesis: Denton, Jerry B. Relationship between the chemical composition of aquatic plants and water quality. M.S. Thesis, Auburn University 78 pp. 1966. 55 RESULTS AND DISCUSSION Studies concerned with chemical and physical characteristics of water in natural lakes have been carried on by limnologists for more than three quarters of a century. These scientists have developed a tremendous volume of data from which they have evolved some very complicated theories relating to the interacting systems operating within these bodies of water. Since an effort has been made to study only those bodies of water which are in as natural a condition as possible, the science of limnology has not concerned itself with those systems operative in man-made impoundments. In fact, data on rivers and their impoundments are largely, and purposely, ex- cluded from the comprehensive reviews published by Hutchinson (1957 and 1967). Complimenting the development of the science of limnology has been the evolvement of the science of waterworks and sewage technology. These researchers have been concerned primarily with the industrial and domestic needs and the public health aspects as related to waters of rivers and impoundments. Thus, this latter group was concerned mainly with use of rivers and impoundments as water sources and effluent disposal areas. Each of these groups has produced a profound influence on the thinking and training of scientists and technicians. One group being oriented toward a condition where man's influence on the environment 56 was excluded, the other where man utilized the water and ignored his influence on the environment. Thus, the dilemma of pollution today is largely a result of lack of understanding of dynamics of chemical- physical-biological interactions within streams and their impoundments. It must be remembered, however, that large impoundments in the United States have been created since World War I and that public utiliza- tion of these impoundments did not start until well after the end of World War II. Thus, the need for an understanding of these bodies of water is of rather recent orgin. Most of the techniques and basic knowledge developed by the two aforementioned groups of scientists are applicable to the solution of many problems in these impoundments today. In other cases the available techniques are either so inaccurate or insensitive as to provide unreliable data for the solution of many biological problems. Aquatic biologists have generally accepted these techniques as providing the needed measurements of environmental parameters and have not been critical of the inadequate results that have been obtained. Instrumentation has been developed which has been or is capable of being adapted to the analytical needs of the aquatic biolo- gists. Full utilization of these modern techniques must be adopted by biologists if they plan to keep abreast with knowledge to maintain and improve our surface water resources. The data presented in the following sections of this report will be concerned with those parameters believed to be essential to our basic understanding of the environment within a large stream- 57 multipurpose impoundment. Several parameters known to be important in such a study have not been adequately sampled or evaluated due to lack of sufficiently accurate and rapid detection techniques. Those areas needing technology developments will be pointed out in the text. Chemical and Physical Characteristics of Water Data collected on a number of physical and chemical characteris- tics of the waters from the various sections of Lake Eufaula during the periods May to November, 1965, March to November 1966, and January to October 1967 have been averaged by stations and depths for each year. Averaged data for each station and depth within the upper (river-run) region, within the middle (upper inundated) region, and within the lower (wider and deeper) region of reservoir are tabulated separately. Also shown in these tables are data from those creeks entering the reservoir within each of the regions. These detailed tables are included in the Appendix. The dynamics of each of the parameters measured in these waters will be discussed in following sections. Temperature and Dissolved Oxygen (D.O.) - Temperature and baro- metric pressure have direct effects upon the solubility of oxygen in water. Temperature and oxygen solubility vary inversely, whereas barometric pressure and oxygen solubility vary together. Under field conditions temperature is the most variable as well as being the most influential factor affecting oxygen solubility. The presence or absence of D.O. in water also exerts an influence upon the solubility of other elements and compounds that may be present in suspended matter or adsorbed onto the surface of the lake bottom. Thus, the status of D. 0. predetermines the concentra- tion of many other chemicals within the body of water at any given time. Information on water temperature and D. O. concentration character- istics in streams and impoundments is of prime importance to the fisheries biologists. These two water quality criteria are the pri- mary considerations in setting the water quality standards by State and Federal Water Pollution Control panels. In Lake Eufaula, individual determinations of temperature and D. O. varied widely from surface to bottom, from station to station, and from one sampling date to another. Since these are highly variable factors and since it is impossible to present each set of individual determinations, examples to illustrate these different conditions will be used. To facilitate utilization of data on temperature and D. O. in discussions, in later sections, they have been averaged by stations, depths and years for each lake portion'(Appendix Tables lA, 1B, 1C), and these data have been further summarized for comparative purpose in Table 1. In the discussion of these two criteria for Lake Eufaula, an attempt will be made to illustrate the dynamic situation that can exist in a warm water, multi-purpose impoundment on a large stream. During the colder months of the year there were sufficient water flows and mixing to give fairly uniform temperatures and dissolved oxygen concentrations in waters at all depths throughout the reservoir. As an example, there was a difference of less than 30 from surface 59 Table 1 Averaged temperature and dissolved oxygen concentrations of Lak-e Eufaula waters by regions and depths for 1965, 1966, and 1967. Yr. Component 65 66 67 65 66 67 65 66 67 Cc 02 ppm OC 02 PPM C 02 ppm c 0 OS ppm 0 2 ppm 0 PPM 02 PPM I0 c 02 PPM 0 r 20' 29.6, 6.59 25.5 6.77 24*7 6.95 26.0 6.20 28.7 6.69 27,1 7.35 30.5 7.63 2900 6.84 28.9 5.17 23.0 6.27 23.8 6.65 25.0 3.82 26.7 4.926 25.2 4.73 28.,4 3.44 27.2 4.66 40' 28.*8 5.15 25.7 4.97 26.1 6.67 24.6 2.72 26.4 ' 3.34 260.0 3.16 27*3 1.61 26.6 3,.28 60' 25.2 2.42 26.1 2.41 24.9 3.51 26.5 25.7 2*.50 Region Upper Middle Lower 27.3 25.2 24.4 . 24.5 8.37* 4.65 2.do18 1.32 1.12 Super-saturated with D.0. to 80-foot-depth, and less than 3 ppm difference in D.0. concentra- tion for the same location in mid-fall of each year of the study (Figures 5, 6). With the onset of warm weather, water temperatures began to vary with depth and so did the D.O., concentration. Usually by late May surface water temperatures were exceeding 28CC and stratification of the deeper waters in lower region of the reservoir had occurred 26.2 1.91 26.6 1.16 L ~n 3 8:0' 0' 20' 60 Figure 5. Dissolved oxygen concentration pattern in Lake Eufaula waters in early November. 61 Figure 6. Water. temperature pattern in Lake Eufaula in early November. and moved upstream at a rather rapid rate so that by mid-June it reached areas with water depths of approximately 60 feet. Under hot weather conditions and normal river flows, stratification would proceed to its most upstream detectable point, approximately 45 river miles above the dam where water depths were 45 feet, Incidentally, this initial stratification point is in the vicinity of a paper mill effluent discharge outlet which is at the 40-foot depth level (bottom of river) of the reservoir. During mid-summer stratification, D.O. concentrations of 1 ppm were found at depths less than 20 feet in mainstream sector of reservoir. Water temperatures under those severe hot weather conditions varied from 5S to 80C from surface to 80-foot depths. Such conditions are illustrated in Figures 7 and 8 for August, 1965. The paucity of phytoplankton growths in surface waters probably accounts for these small differences in temperature in these deeper waters. In contrast, tributary streams with heavy phytoplankton growths had temperature differences as great as 5C from surface to 15-foot depth; however, the D.O. concentration at this depth was significantly greater (2.5 ppm or more) than in the reservoir proper. It is significant to note that during worm weather mainstream surface water D.O. concentrations seldom approached and almost never ex- ceeded saturation. This condition of sub-saturation of D.O. in sur- face waters in the main impoundment is not understood, but it is suspected to result from the interaction of current, wave-action, and turbidity upon phytoplankton production. Changes in weather conditions during the summers of 1965 and 63 DEPTH 4 60 WATER TEMPERATURES oC AUGUST 20,1965 80I o' Figure 7. Water temperature pattern in Lake Eufaula in mid-August. Figure. 8. Dissolved oxygen concentration pattern in Lake Eufaula waters- in mid-August. 64 65 1966 produced drastic changes in D.O. concentrations. On one occasion during mid-August surface waters contained 9 ppm D.O. and bottom waters at 40 feet contained 3.5 ppm D.O. Three days later, after a period of cloudy, rainy weather, the waters at this same location contained 3.5 ppm D.O. from surface to bottom of river. The causes of such reductions in D.O. concentration are not known. However, following such overturns, an uninterrupted period of 7 to 14 hot days would produce another stratified condition over most of lower 2/3 of reservoir. In contrast to the drastic chemical changes that occurred throughout the summers of 1965 and 1966, the summer of 1967 did not produce hot weather of sufficient duration to cause complete D.O. depletion in any mainstream area of the reservoir. During the first half of September of both 1965 and 1966, theentire reservoir overturned because of a cooling of the surface waters of approximately 2*C. Data on the pattern of the overturn in 1966 were obtained by chemical analyses and by fluorescent dye. On September 6 a dye study was begun to determine the time-of-flow of water at 70+ foot depth in the lower portion of reservoir (1) . The dye was pumped down by hose to a release point 6 feet above the river bottom at 3 locations (points A, B and C) as indicated in Figure 9. The movements of these clouds were followed (1) Complete data were given in Report on Contract No. WA-66-10 U.S.D.I., FWPCA, Time-of-flow and dispersion studies on Walter F. George Reservoir. 66 Figure 9. Dissolved oxygen concentration patterns and dye patterns in lower portion of Lake Eufaula during period September 6-12, 1966. 67 for the next 7 days. During the 96 hours following application, each of the two lower clouds (B and C) moved downstream in a 10- foot thick cloud for a distance of approximately 6 miles. The up- stream cloud (A) moved 0.25 mile downstream during 24 hours following injection. It then reversed its movement and traveled in an upstream direction for next 72 hours. On September 9 this dye cloud had progressed through two parallel bridges to a point 2.5 miles upstream from the point of injection. The thickness of this cloud was appro- ximately 20 feet in contrast to the 10-foot thickness of the down- stream clouds indicating that more turbulence occurred in this back current situation than occurred in normal downstream flow. Data on water temperatures and D.O. concentrations existing on September 9 for this region of the reservoir are given in Figures 9 and 10. These data are representative of the conditions that existed throughout the first 4 days of this study. During the next 48 hours the moderate easterly wind, which had already plagued the research operations for 72 hours, intensified and became cooler. Thus, by September 12 the majority of the lake had already over- turned or was in process of overturning as indicated by Figure 9. Monitoring of areas occurpied by 2 lower dye clouds indicated complete dissipation of the fluorescent dye. D. O. and temperature monitoring also indicated that bottom waters had mixed with upper waters. Monitoring of the uppermost edge of the upstream cloud (A) with the fluorometer indicated that this cloud had moved toward the sur- face to the 45-foot letel, and that non-fluorescent waters had under-run the cloud. Dissolved oxygen monitoring of this area confirmed Figure 10. Water temperature patterns and dye patterns in lower portion of Lake Eufaula during period September 6-12, 1966. 68 69 the fluorometer findings for the area still occupied by dye had 0.5 ppm D.O. while waters below and above this 45-foot level had waters with 2 + ppm D.O. (see Figure 9). In addition to confirming the findings of the YSI oxygen and temperature probe concerning stratification and overturn, this fluores- cent dye also established that density currents do exist under strati- fied conditions in the deeper water areas of this reservoir. However, the most significant aspect of this deep water phase of dye research was the detection of upstream currents created by the 2 causeway type bridges on this reservoir. Information on time-of-flow of the reaches of reservoir between river miles 141 and 110, and river miles 87.7 and 75.1 are given in Figure 11. Under relatively normal mid-summer weather and flow- rates the average rate of flow in the river-run sector of the reser- voir was 0.41 mile per hour. In the lower sector of the reservoir the deep water time-of-flow was approximately 0.08 mile per hour. Based upon averaged inflow and outflow data for this reservoir (Appendix Table 6), and taking into consideration the loss by seepage and evaporation (Appendix Table 7), there would be a complete ex- change of water volume (926,000 acre-feet) within approximately 80 days. This would have produced an averaged time-of-flow within the lower portion of approximately 1 mile per 24 hours, or 0.04 mile-per-hour. Comparing the observed with the calculated flow rate indicates that the water in lower depths of the river channel was traveling at twice the calculated rate. This appears to further in- dicate that a density current does exist in this reservoir under hot weather conditions. 70 Figure 11. Time-of-flow for fluorescent dye in various portions of Lake Eufaula during August and September, 1966. 71 The time-of-flow in a downstream area below Columbia dam (see Figure i), as determined by use of fluorescent dye, is given in Figure 12. Resistivity (or Conductance) - Averaged data on resistivity of waters from different stations and depths within each lake portion are given in Appendix Tables 1-A, 1-B, 1-C. While these data are expressed 3 as ohms/cm , they might readily be converted to conductance values by obtaining the reciprocal of each value. The summarized resistivity data presented in Table 2 indicate two features of Lake Eufoula waters. First, these are very soft waters. Second, changes in resistivity values did not appear to be associated with any marked changes in composition of any one element, but apparently resulted from a change in concentration of several elements. Slight decreases in resistivity values for bottom waters within creeks (Table 3) could be associated with increased concentrations of Ca in these waters. Figure 12. Time-of-flow of fluorescent dye in Chattahoochee river below the Columbia Dam. 72 73 Table 2 Averaged resistivity values of Lake Eufaula waters by regions and. depths for.1965, 1966,. and 1967 Region Upper Yr. Component 65 66 67 Resistivity 65 Middle 66 67 Lower 65 66 67 Averaged ohms/cm 3 for given depths 0', 20' 40 # 600' 80f 15153 17289 17699 17185 16716 17441 1652.2 17355 16800 14788 17281 17233 17657 17127 17044 15700 17891 16700 15843 18416 17150 17483 16446 18055 16200 17380 16400 16250 15945 16560 14633 16657 16900 17957 16000 x.550 Table 3 Averaged resistivity values for waters at*different depths in tri- bu tary creeks of various-regions of Lake Zufaula in 1965, 1966, and 1967 Region Uppe r 65 66 67 Resistivity 65 Middle 66 67 Lower 65 66 67 Averaqed ohms/cm 3 0' 18500 17065 18608 14450 16555 16482 18625 17750 for given depths Near bottom 19450 16850 13705 12395 14900 14050 18866 - --- I y - - 74 pmo - The averaged data on pH for each station and depth within each lake region for each year are given in Appendix Tables 1-A, 1-B, 1-C. Surface water pH's were fairly constant for the entire length of main reservoir throughout the 3-year period as shown below. Of more importance was the fact that at no time did these pH values vary beyond the range from 5.5 to 9.0. Deeper water areas within the reservoir showed a slight decrease in pH values, but these were still within the safe and desirable range for aquatic life. It should be noted that the pH range within creeks was no wider than for the main reservoir. Region Year Averaged pH for given depths 0 20' 40' 60' 80' Upper 65 7.25 6.65 6.74 66 7.40 7.15 7.10 67 7.28 6.60 6.51 Middle 65 7.26 6.72 6.78 6.75 66 7.67 7.18 7.08 7.03 67 7.44 7.09 6.79 6.85 Lower 65 7.90 7.05 6.79 6.66 6.90 66 8.00 7.52 7.27 7.20 7.19 67 7.75 6.75 6.45 6.80 6.35 75 Potassium and Sodium - The data collected on the concentrations of K and Na in waters of Lake Eufaula and its tributaries throughout the 2 1/2-year study period are summarized in Appendix Tables 2A, 2B,and 2 C . While some variations in concentrations for each of these elements existed from station to station for each year, these variations are of such random nature as to indicate only changes that might be associated with river-flow-rates (dilution). The averaged K concentrations, as ppm, by depths for each re- gion and year were as follows: K ppm Region Year 0' 20' 40' 60' 80' Upper 65 1.82 2.07 1.75 66 1.93 1,85 2.07 67 1.74 1.15 2.28 Middle 65 .65 1.74 1.81 1.88 66 1.92 1.94 2.00 1.98 67 1.43 1.35 1.45 1.46 Lower 65 1.60 1.63 1.62 1.68 1.55 66 1.81 1.95 1.75 1.97 1.54 67 1.40 1.42 1.43 1.05 2.00 The average K concentrations, as ppm, by depths for tributary streams within each region and year were as follows: K ppm Region Year O' near bottom Upper 65 1.00 - 66 2.58 1.81 67 1.36 1.44 Middle 65 2.10 1.99 66 1.63 1.69 67 1.30 1.36 Lower 66 1.63 1.61 67 1.15 .95 76 Limited data on seasonal trends of K concentrations for 1967 indicated there .was .a slightly greater concentration of this element during summer period than for the spring period as shown below: Spr ing Summer 0' - 40' 0' 20' 40' 60'+ K ppm 1.33 1.74 1.64 1.99 1.53 These differences might also have been due to dilution as mentioned previously. The averaged Na concentrations as ppm by depths for each region and year were as follows: Na pPm Region Year 0' 20' 40' 60' 80' Upper 65 6.49 6.50 5.80 66 5.10 4.40 4.49 67 5.38 4.90 5.36 Middle 65 4.00 3.96 4.08 4.12 66 4.91 4.91 4.91 4.29 67 5.34 5.10 5.22 5.32 Lower 65 7.04 7 .86 7.54 4.12 5.88 66 4.49 4.10 4.20 4.55 3.52 67 5.33 5.31 5.00 4.19 5.25 The averaged Na concentrations as ppm by depths for tributary streams within each region and for each year were as follows: Na ppm Region Year 0' Near bottom Upper 65 2.00 66 5.96 4.29 67 3.83 4.03 Middle 65 6.00 6.68 66 3.46 3.28 67 4.88 4.28 Lower 66 3.31 2.60 67 5.26 3.09 77 Comparative spring and summer concentrations of Na in Lake Eufaula are given below: Spring Summer 0' 40' 0' 20' 40' 60'+ Na ppm 4.50 5.73 5.35 5.35 4.89 Dilution again is suspected in causing these differences in Na con- centrations. With both elements, differences in solubility constants associa- ted with temperature might help account for the decreased concentra- tions in cooler weather. 78 Calcium, Magnesium and Total Hardness - Data collected on calcium and magnesium contents in waters from Lake Eufaula and its tribu- taries during 1965, 1966 and 1967 indicated some degree of variation between depths and stations but there were no drastic changes in yearly averages (Appendix Tables 2-A, 2-B, 2-C and 3-A, 3-B, and 3-C. During both 1965 and 1966 the total hardness of these river waters was determined by the EDTA compleximeteric method (Table 4) and then calculated from the Ca and Mg contents of these waters. These averaged data on total hardness of waters throughout the re- servoir for each year and for each method of determination are shown graphically in Figures 13 and 14. The variations between EDTA and calculated (from Ca + Mg content) total hardness for any given location are not so great as might be expected at first glance. Suffice it to say that these lake waters are in the very soft category; that portion of calculated total hardness attributed to Mg was consistently between 4.25 and 5.5 ppm CaCO 3 equivalent, while the portion attributable to Ca was responsible for the evident variation. The causes of the disagreement in the two methods of determination are not known, but it is suspected that certain naturally occurring constitutents of water in some way interferred with color changes associated with the compleximeteric EDTA method. Since total hardness was of little value in this biolo- gical study, its determination by EDTA titration was limited in 1967. 79 Table 4 Averaged Calcium, Magnesium, and total' hardnes's concentrations of Lake Eufaula waters by regions and depths for 1965, 1966 and 1967 Region Year Averaged concentrations in ppm UO, 20' 40' for g i'ven depth. .60 ' 80'1 Uppe r 65 66 67 Middle 65 66 67 Lower 65 66 67 (1) DTA otalhardness, expressed as ppm CaCO, Ca Mg E DTA Ca Mg EDTA Ca Mg EDTA Cal Mg EDTA Ca Mg EDTA Ca Mg EDTA Ca M g EDTA Ca M g EDTA Ca Mg EDTA 3.95 1.,25 16.73 4.57 1.10 14.73 2.97 1.12 13.11 3.67 1 .42 15.79 4.46 1.22 14.52 3.44 1.14 13.18 4.25 1.39 15.77 4.41 1.18 15.20 3.62 1.22 14.75 6.42 1.23 15.20 4.77 1.15 13.82 3.52 1.14 14.12 3.88 1.38 15.82 4.48 1.20 14.63 3.41 1.16 13.58 4.34 1. 44 16.13 4.85 1.16 15.57 3.70 1.24 14.25 3.78 1.33 15.40 4.72 1.17 14.59 2.72 1.06 13.62 4.36 1.30 15.57 4,64 1.17 17.28 3.66 1.41 13.25 4.63 1.40 17.025 4.57 1.19 15.22 3'.53 15.00 4.48 1.50 1725 1.16 17.73 2.97 .16 13.61 4.92 1.35 18.o5,3 4.-85 1.19 16.61 4.32 1.10 17,50 5.34 1.28 21. 56 5.33 1.12 17,90 3.82 1.26 16. 50 rr u Ir. rr (1) EDTA = total 80 MUSCOGL AY CLA Vs '11L5KE FAEIL 12 /F BWIG 0 PPMIT Ek 6r d h musco E' LA 20 M. DEE "-I. co/ -Mi WEN.- -0 5 - Ia E u PPPM 40A PPPM 2020 DDEEP 15-5 P96PPP DEEMPTH.- DE 15 1- Figure 13. Averaged total hardness of. Lake Eufaula waters in 1965 as determined by EDTA titration and cal- culated from calcium and magnesium content. / - ~~;4 b Ca A f-A 20' DEEP 40' DEEP 1966 AVERAGED TOTAL HARDNESS AS PPM CaCO 3 EDTA T.H.-- Co + Mg TH -- Figure 14. 81 PPM SURFAQ l5 A I -_ - PPN PPM 8d DEEP Averaged total hardness of Lake Eufaula waters in 1966 as determined by EDTA titration and calculated from calcium and magnesium content. I 82 One other interesting feature in each of these figures is the change in total hardness concentrations associated with each area in the vicinity of bridges located at mile 98, at mile 120, and at mile 145. These variations apparently resulted from current turbu- lence created by bridge piers located at various points across the river. However, the mouths of major tributary creeks are also located in these areas, and they may have contributed to these changes in concentrations (Table 5). Data collected during 1967 and shown below indicated that there was an approximate 40 percent decrease in Ca concentration in waters during summer than was present during the early spring. Spring Summer 0 - 40' 0' 20' 40' 60' Ca ppm 4.04 2.55 2.61 3.04 3.59 Mg ppm 1.18 1.11 1.16 1.12 1.19 EDTA, ppm CaCO 3 15.30 13.65 13.80 13.95 15.52 Previous research in plastic pools had indicated that such a condition could occur. However, further collection of data on Ca and Mg con- tents of these waters on a year around basis is needed to verify this cycle and define its characteristics. Comparative data on the Ca and Mg concentrations in the Chatta- hoochee river arm of Lake Seminole are given in Tables 6, 7, and 8 These data indicate an increase in Ca concentration in water as the river proceeds through the limestone sink areas near the Alabama, Florida, and Georgia state lines. The Mg on the other hand does not increase indicating that these lime sinks are practically pure CaCO 3 83 Table 5 Averaged calcium, magnesium and total hardness concentrations of waters at different depths in tributary creeks of various regio-ns'-- of Lake. Eufaula in 1965, 1966, and 1967, Region Year Upper 65 66 67 Middle 65 66 67 Lower Component Ca Mg EDTA Mg EDTA Ca Mg EDTA Averaged concentrati.onsin pp2m atgiven depth 0f Near bottom 4.92 11.55 20.50 4.145 1.25 14.85 4.50 1.07 13.00 4.14 1.35 21.15 7.40 1.05 18.28 4.16 14.75 4.27 1.07 16.00 3.00 1.06 15.00 Ca Mg EDTA Ca Mg EDTA Ca E IYIA Ca Mg EDTA Ca Mg E Drf A Ca Mg EDTA 65 66 67 5.00 1.20 14.33 4.57 1.07 13:00 6.19 1.29 22.61 9.82 .17 24.31, 5.90 1. 11 19.20 1.10 34.95 4.60 18.25 84 Table 6 Averaged composition of waters from various regions of Lake Seminole in 1965 Depth, feet 0-30 0-20 1:* 7.30 6.84 vbta alk, ppm CaC0 3 28.26 58.1 Resistivity, ohms/cm 14052 7911 Total hard, ppm CaCO 3 26.37 56.6 )t- Ca, ppm CaCO 3 7.59 19.8 Mg, ppm 1.18 1.13 fO Na, ppm 7.36 7.6 K, ppm 1.58 .89 Zn, ppm .058 .013 Cu, ppm .024 .039 Fe, ppm .24 .444 Mn, ppm .023 .022 N, as ppm NH 3 .319 .194 P, ppm .020 .044 Total C, ppm 14.08 17.09 Total chlorides, ppm 5.85 5.43 Total Sulfates, ppm 6.47 2.78 Turbidity, nephlos 26.5 24.4 85 Table 7 Averaged composition of waters from various regions of.Lake Seminole in 1966 Depth, feet PH Total alk, ppm CaC0 3 Resistivity, ohms/cm Total hard,. ppm CaC03 Ca, ppm CaC0 3 mg, ppm Nal ppm K, PPM Zn, ppm Cu, ppm Fe, PPM Mn, ppm N, as ppm NH 3 P" PPM Total C, PPM Soluble C,ppm Particulate C, ppm Total chlorides, ppm Total Sulfates, PPM Turbidity - JTU 0-10 7.64 46.43 8512 45.2 14.6 1.23 2.89 .73 .023 004 .38 .019 .251 .01 0-30 7*.43 23.62 16418 20.37 7.19 1.09 5.04 1.60 .033 006 .72 .038 .209 008 14.43 8.66 3.97 4.08 8.44 17.0 si 0-10 7.73 39.84 11900 37.10 18.95 .91 1.78 .48 .001 .055 045 16,88 3.5 2.0 0-20 8.14 82.2 67 18 80.63 37.68 . 77 2.28 .62 .011 .003 .083 .07 .29 .001 25.0 10.44 3.67 2.35 0-30 7.66 33.75 11194 34.2 12.82 .94 2.74 1.22 .166 .013 2.09 .043 .104 .028 16.9 9.4, 7.36 4.22 5.94 22.6 4.02 3.5 4.4 86 Table 8 Averaged composition of waters from various regions of Lake Seminole in 1967 " L r Depth, feet 0-25 0 -15 0-25 0 0 0.20 pH 7.28 7.05 7.38 7.59 - 6.98 Total alk, ppm CoCO 3 25.0 54.04 81.06 56.53 48.33 44.50 Resistivity, ohms/cm 13492 8435 7243 9323 10700 9680 EDTA hard, ppm CaCO 3 52.25 83.2/ 50.87 - 49.25 Ca, ppm 4.4 .7.55 23.60 18.1// 15.4/ 10.44 Mgj, ppm 1.25 .93 .49 .91 1.55 ./8 Na, ppm 5.6/ 2.52 2.15 2.53 2.31 3.12 K, ppm 2.21 .43 .3u .49 .39 .6o Zn, ppm .161 .013 .019 .075 .022 .020 Cu, ppm .015 .007 .007 .024 .042 .004 Fe, ppm .185 .055 .140 .072 .060 .230 Mn, ppm .034 .022 .014 .026 .017 .013 N, as ppm NH3 .188 .215 .165 .225 - .190 P, ppm .103 .068 .037 .032 - .046 CT, ppm 12.58 18.44 26.62 18.42 23.00 14.90 C.C0 2 , ppm 10.38 9.20 12.00 12.44 17.30 6.60 Cs, ppm 8.21 16.90 20.48 13.80 9.50 12.55 Total chlorides, ppm 6.85 5.47 5.45 5.47 - 5.65 Total Sulfates, ppm 6.00 3.10 2.62 2.75 - 3.60 Turbidity - JTtJ 5.16 1.34 1. 74 1.40 1. 87 5.20 Sr, ppm .007 .012 .015 .025 .012 .013 Pb, ppm - .180 .032 .014 .071 - 87 in composition. Additional data on the Ca and Mg concentration in the Flint River and Spring creek arms of Lake Seminole are also given in-Tables 6, 7, and 8 . These data are presented for later comparative use in regards to aquatic plant chemical composition from various regions of both reservoirs. Data on ranges of concentrations of Ca and Mg in Bartlett's Ferry Reservoir are given in Table 9. These data indicate the same general trends in Ca and Mg contents of Chattahoochee river waters as has been presented for Lake Eufaula. 88 Table 9 Ranges in composi.tion of waters from Bartlett's Ferry Reservoir during 1967 Depth, feet JTU pH Alk. ppm COCO 3 Ohms/cm 3 EDTA hard, ppm CaCO 3 Ca ppm Mg Na K Zn Cu Fe Mn N as NH 4 P CT Pb Sr .0 10-72 7*8-10.2 1500-17. 5 17100- 21000, 14.5-15.0 3.2-6.*2 5.6-6.8 1. 12-1.42 .17-10*83 o 1860.20 .15-1.50 001-*10 014-.26 .005- .36 70.0-11.2 .005- 015 25. 6.8-7.9 13.75-16.25 175000-18500 15.0-1695 2.9-5.0 1.07-1.15 6.0-7.2 1.2-1.3 .2-1.75 .19.0 *10-1.70 .03- 21 .0740 40 .'0057-o.19 9 .0-10.6 o05-*18 o.12- .016 L~LI JI I -L 89 Alkalinity - The averaged data on alkalinity, expressed as ppm CaCO 3 , for each station and depth within each lake region are presented in Appendix Tables 3-A, 3-B, and 3-C. Alkalinity, showed a decline in concentrations throughout the study period. The most drastic change occurred between 1965 and 1966 as indicated in Table 10. This decline in alkalinity is believed to have resulted from a reduction in decomposition of flooded vegetation. 90 Table 10 Averaged total alkalinity, as ppm CaCO 3 , conceontrations of Lake Eufaula waters by regions and depths'for 1965, 1966, and-1967 Re gion Year Uppe r 65 66 67 Middle .65 66 67 Lower 65 66 67 Averaged alkalinity, ppm, for given depths .020 40' 60' 80' 24.50 18.58 18.70 20.86 18.05 17.83 25.62 180.,93 19.06 26.70 17.07 16.67 21.*44 17.11 18.33 20.73 17.o96 19.06 23.03 17.13 17. 58 23.12 17.74 1.8.75 23. 44 19.07 19.06 27.85- 17.42 18.12 23.28 20,27 20.00 29.42 23.50 18.75 ()Alkalinity Total alkalinity, titrated to PH 5.2 and expre ssed as ppm CaCO 3 91 Turbidity - The averaged measurements on concentrations of suspended matter in lake waters, expressed as nephlo units for 1965 and as Jackson turbidity units (JTU) for 1966 and 1967, are given in Appendix Tables 3-A, 3-B, 3-C. To better understand the changes in turbidity associated with portions and depths of this reservoir, these averaged data are summarized below: Depth Region Year 0' 20' 40' 60'+ Upper Nephlo 65 20.8 29.7 25.0 JTU 66 13.3 20.4 30.7 JTU 67 14.8 16.3 20.7 Middle Nephlo 65 36.9 43.7 57.1 51.0 JTU 66 11.6 20.2 19.2 21.3 JTU 67 10.6 12.8 11.9 15.8 Lower Nephlo 65 11.5 18.4 23.2 40.0 JTU 66 4.7 6.2 7.2 8.9 JTU 67 3.6 4.7 6.7 8.7 From these data it is readily evident that the suspended matter in upper and middle regions was much greater in waters at all depths than in lower region. The values for the upper and middle regions of the reservoir might have been slightly higher or lower depending upon the suspended matter content on a particular sampling date. Based upon these data it would appear that turbidity has de- creased over the 3-year period of this study. The decrease may also be a chance occurrence, but it is a fact that during the early 1930's the waters in upper region often approached 400 JTU's. Thus, there has been a great stabilization of soils in this drainage area in recent years as evidenced by these 3-year data. 92 All related data plus visual observations on lower region of Lake Eufaula throughout this study period indicate that surface water turbidity was due to microscopic plant growths, but at lower depths a major portion of the turbidity resulted from colloidal materials, such as iron, and decomposing plant materials with a smaller amount being due to soil colloids and other particles. Averaged data on turbidity of surface and near-bottom waters of tributary streams within each portion of reservoir during 1965, 1966, and 1967 are given below. 93 Region Year Averaged turbidity for given depths O' near bottom Upper 65 Nephlos 33.0 66 JTU 16.0 20.0 67 JTU 9.2 20.0 Middle 65 Nephlos 14.5 21.9 66 JTU 8.4 15.2 67 JTU 8.1 21.4 Lower 65 66 JTU 5.7 21.2 67 JTU 6.2 27.1 Iron (Fe) and Manganese (Mn) - Data collected on Fe and Mn con- centrations in waters of Lake Eufaula during 1965, 1966, and 1967 varied for different depths and stations as indicated by the averages given in Appendix Tables 4-A, 4-B, 4-C. At times there were even greater variations between sampling data which is not readily evident from data in these tables. The data given for 1965 were obtained from samples filtered through No. 42 filter paper while those data for 1966 and 1967 are for unfiltered waters (Table 11). However, during 1966 and 1967 determinations of Fe were made on unfiltered and filtered (through 8 u millipore filter) waters. The differences in these Fe contents for 1966-67 are shown in Table 12. They appear to be of the same general order as the differences between the 1965 and 1966-67 data (Table 11). The higher concentrations of Fe indicated for the upper and middle regions of the reservoir (in 1966-67) were due primarily to iron carried by mud particles. This provides support for the theory 94 Table 11 Averaged iron and manganese concentrations of Lake Eufaula waters by regions and depths for 1965, 1966, and 1967, Depth Region Upp er Middl e Lower Year Component 65 66 67 6.5 66 67 65 66 67 Fe p pm Mn Fe Mn Fe Mn Fe Mn Fe Mn Fe Mn Fe Mn Fe Mn Fe Mn 0' e125 .030 .556 * 079 .496 .023 .132 .012 .587 S0,73 .016 *070 .045 *187 .050 * 107 * 011 20t .110 .038 .850 o 102 .477 .038 .155- * 024 .870 .063 .373 .031 o120 .033 .200 .033 o018 4O .117 .021 780 .152 740 040 .160 .022 *983 .30-5 .476 .064 ,141 .038 .345 145 205 048 60' 80' .357 .174 1,173 .323 .692 .081 .061 .135 .562 .225 400 .105 .260 .67 1.290 950 *175 0O50 95 Table 12 Averaged percentages of removable Fe and Mn from waters of Lake Eufaula as determi.ned from concentrations determined for raw and filtered waters Region Year ppm Fe raw water ppm Fe Upper '66 '67 Middle ' 66 '67 Lower '66 '67 Creeks '67 (0') (bottom) .816 o885 .670 .619 *573. .187 .415 1 .403 filtered .461 .231 .346 .167 .316 .061 .152 .308 water % removable Fe 4305 73.9 48.4 73.0 44.9 67.4 63.4 78.1 R o Year.ppmMn raw water ppm Mn Upper ' 66 '67 Mi ddl e '66 '67 Lower '66 '67 Creeks '67 (0') (bottom) .121 .036 .085 .056 .186 .4034 .031 .079 filtered .019 .005 *050 O016 .076 .012 .005 .052 water % removable Mn 84.3 86.1 41.2 71.4 59.3 64.7 83.9 34.2 96 that the portion of reservoir above mile 98 functions as a settling basin and that the portion between miles 98 and 75 is a clearer water area. It will be noted that at 20 + foot depths the data indicate a relatively greater concentration of Fe than was detected in surface waters. Some portion of this increased Pe content was due to underrun- ing of muddy waters in the lower half of the reservoir. However, much of this increased concentration is believed to have resulted from suspension of colloidal forms of iron. This situation seemingly was enhanced by D.O. deficiency which converted the precipitated ferric (Fe ) form on the bottom to soluble ferrous (Fe ++) forms, allowing more Fe to be in solution, then when an aerobic condition occurred the ferrous iron was converted to colloidal ferric iron which remained in suspension for indefinite periods. Manganese did not occur in either the concentrations or in the some general trend as was evidenced for iron. There was no conclusive evidence that manganese content of water was associated with muddiness. In fact, the data seemingly indicates that in sufface waters muddiness decreased the Mn content, and that increased concentrations of Mn were associated with growths of phytoplankton. In deeper water areas, D.O. deficiency apparently brought about the conversion of precipitated manganic (Mn ++) form to the soluble manganous (Mn +) form, but only in limited amounts when compared with iron under the same conditions (Table 12). Unlike the iron, when the stratified area became aerobic, the manganous form again precipitated on the hydrosol. 97 The following are averaged ratios of Fe to Mn in Lake Eufaula waters for 1965, 1966, and 1967: 1965 3.35 to 1.0 1966 4.12 to 1.0 1967 11.54 to 1.0 These ratios indicate that stratification was much more evident in 1965 and 1966 than it was in 1967. Zinc and Copper - The averaged concentrations data on Zn and Cu are summarized for each year in Appendix Tables 4-A, 4-B, 4-C. While the total concentrations are generally in the ppb range, the variations are often many-fold different between years for same station and between stations for a given year. The data for 1965 were all obtained on waters that had been passed through No. 42 filter paper, thus accounting for generally lower values of Zn reported in the tabular data particularly those for the river-run areas of the reservoir. In 1966 and 1967 the data shown in aforementioned tables are for Zn concentrations in raw river waters. In each of these years the waters were passed through 8 u millipore filter and the concentration of Zn in the filtrate was obtained. In order to more fully understand the data on filterable Zn from those river waters, the averaged removal of Zn for the upper, middle, and lower regions of reservoir are given below: Region Year ppm Zn raw water ppm Zn Upper '66 .062 '67 .040 Middle '66 .070 '67 .749 Lower '66 .027 '67 .426 Creeks '67 0' .038 Bottom .052 filtered water % removable Zn .024 61.3 .022 45.0 .026 62.9 .434 42.1 .011 59.3 .227 46.7 .012 68.4 .016 69.2 It is most interesting to note that Zn concentrations increased in the middle portion of reservoir in 1967 and that this increase carried over into lower portion. The suspect source of this Zn was from condenser, and other piping of a new paper mill located at the extreme upper end of middle portion. This concentration will be expected to decrease with time since the amount of soluble Zn in tubing, etc., should decrease after several months flushing with water. The averaged Cu content of raw and filtered lake waters and per- cent of removable Cu by filtration are shown below: Year ppm Cu raw water ppm .Cu '66 .019 '67 .024 '66 .025 '67 .011 '66 .024 '67 .028 '67 0' .017 Bottom .016 filtered water % removable Cu .014 24.3 .017 29.2 .015 40.0 .009 18.2 .010 58.3 .015 46.4 .015 11.8 .013 18.7 98 Region Upper Middle Lower Creeks .. OW 99 These data indicate only a random variation associated with overall lake conditions during these 2 years. Nitrogen and Phosphorus - The data collected on N as ammonia (NH 4 ) and P as orthophosphates in waters of Lake Eufaula are summarized in Appendix Tables 5-A, 5-B, 5-C. It is obvious from the analytical methods used that these data did not account for the total N or P content in these raw waters. That considerable variation existed between analyses for each element is evident in each table. The averaged concentrations of N as NH 4 during cool months was slightly less than for the summer months as indicated by the averaged data for 1967: Cool months Summer months O' to 40' 0' 20' 40' 60'+ N ppm .219 .237 .213 .435 .332 Comparative averaged N as NH 4 concentrations by depths for each year were as follows: 0' 20' 40' 60'+ 1965 N ppm .2077 .2463 .2777 .3250 1966 N ppm .2094 .2171 .2728 .3285 1967 N ppm .2365 .2189 .4351 .3132 The increased NH concentration associated with water depth is a normal phenomenon, however, these marked increases at lower depths are also associated with a part of the middle portion and the lower portion of reservoir. The highest value, 0.4351 ppm N as NH 4 at the 40-foot depth in 1967, is believed to have resulted from drainage from a large hog-farm operation on the Georgia bank in middle portion 100 of reservoir. Similar high data on total N have been obtained for this same area in 1966 by Alabama Kraft Company personnel. Comparative data on concentrations of N as NH 4 in tributary creeks on Lake Eufaula were as follows: 0' near bottom 1965 N ppm .135 .229 1966 N ppm .193 .214 1967 N ppm .327 .343 The increased N content of surface waters in main reservoir and in tributary creeks in 1967 can only be attributed to the con- tinuous mixing of these surfaces and lower waters resulting from the cooler weather and lack of stratification. The averaged concentrations of orthophosphates during cool months was several fold less than those existing in summer months of 1967 as indicated by following data: Cool months Summer months O' to 40' 0' 20' 40' 60'+ P ppm .015 .092 .097 .092 .083 Comparative averaged P as orthophosphate concentrations by depths for each year in main reservoir were as follows: O' 20' 40' 60'+ 1965 P ppm .024 .043 .029 .034 1966 P ppm .011 .011 .009 .018 1967 P ppm .067 .070 .063 .082 The explanation of decreased P content of waters during cool weather is unknown, but could have been an interaction between cool 101 water temperatures, excessive clay colloid content of these waters, and increased flow. Averaged data on P as orthophosphate content of surface and near bottom waters from tributary creeks were as follows: O' Near bottom 1965 P ppm .037 .039 1966 P ppm .006 .011 1967 P ppm .049 .069 No logical causes for the decreased P content in main reservoir and in tributary streams in 1966 are known. Total carbon and COo- free carbon - The data collected on the total carbon content of raw waters from Lake Eufaula during period from July 1965 through September 1967 are summarized by stations and depths in Appendix Tables 5-A, 5-B, 5-C. Data collected in 1967 on CO 2 -free carbon content of raw waters are also summarized in the same tables. Trends in total carbon contents of lake waters in 1965 and 1966 are shown in Figure 15. The decrease in total carbon content in river waters above mile 120 in 1966 was assumed to have resulted from the improved sewage treatment facilities put into operation by Columbus, Georgia and Phenix City, Alabama in late 1965. Data on remaining portions of reservoir are practically the same for 1965 and 1966 and are onaly slightly higher than those obtained for 1967 as shown below: PPM~ 15- I0- PPM I 6d DEEP AVERAGED TOTAL CARBON 1965 8 1966 Figure 15. 102 20- SURFACE o0- PPM 15 I0- 2d0 DEEP 40 DEEP __ "'- - PPM 15- 80 DEEP I0- 0 Averaged total carbon contents of waters at various depths for entire length of Lake Eufaula for 1965 and 1966. v I / v'': r .sr. 'r - .. _ r... 103 0' 20' 40' 60'+ 1965 C ppm 12.26 12.46 13.17 11.21 1966 C ppm 11.56 11.17 12.61 13.42 1967 C ppm 10.09 10.11 9.95 10.43 These data all indicate that the domestic, agriculturc industrial effluents entering this reservoir are relativel of organic matter, and more importantly, the condition has each year. The CO 2 -free carbon contents of these lake waters for were the following percentages of total carbon contents of lake waters: al, and y devoid improved 1967 raw upper region 46% middle region 37% lower region 55% The remaining averaged soluble + particulate carbon (CO2-free carbon) contents of these waters were as follows: upper region 5.54 ppm C middle region 6.11 ppm C lower region 4.80 ppm C Based upon CO 2 -free carbon - C.O.D. relationship established by Dr. G. N. Greene of the Farm Ponds Project, Auburn University, these waters had such a low C.O.D. value that they gave a calculated negative value. Further support of this condition was obtained by Alabama Kraft Company Water Quality Laboratory on B.O.D. The average of bi-weekly 5-day B.O.D. tests for the upper and middle regions of reservoir for 1967 was approximately 2 ppm 02. Thus, only 0.6 104 ppm of this C0 2 -free carbon was decomposable into CO 2 . Based upon total CO2-free carbon contents of fertilized ponds these lake waters are very devoid of microscopic plant growth. This condition had already been indicated by presence of relatively large concentrations of soluble NH 4 and P in these lake waters. The tributary streams were also generally low in total CO2-free carbon content as indicated by Table 13. Chemical Composition of Suspended Matter in Water - As previously mentioned, the technique for separation and analyses of suspended matter in lake water was developed in mid-summer of 1967 and only a limited amount of these data are available for inclusion in this re- port. These averaged data are presented in Tables 14, 15, 16 and 17. It is to be noted that these data are in ppm for each element as it occurred in the sample of water. Therefore, these values can be compared directly with raw water and filtered water chemical content. A number of interesting relationships are evident in these data. Since the data are limited, these relationships will have to be considered only as possibilities. Yet, they do indicate that these selected elements vary considerably in the suspended matter of water over distance as well as time in Lake Eufaula. Calcium concentrations in suspended matter decreased throughout main reservoir during August and then increased during September. Similar analyses of phytoplankton removed from ponds during August indicated an even greater decline in Ca content, and only a slight recovery in September. 105 Table 13 Averaged total carbon content at surface and near bottom in streams of 3 regions of Lake Eufaula during 1965, 1966, and tributary 1967 Year Component 65 66 67 65 66 67 65 66 67 CT CT CT cco2 CT CT CT Cco 2 CT CT CT Averaged concentration in ppm at given dePths 0O near bottom C- 10.9 9.5 4.91 21.0 12.7 10.5 6.71 11.0 11.7 6.97 10.9 9.6 4.45 19.7 17.0 13.9 8.32 15.8 17.7 9.07 Region Upper Middle Lower . . Table 14 Averaged chemical element composition of suspended matter collected on August 3, August 9, and August 16, 1967bewn river miles. 120 and,98 0' .401 0' 20' 40' August 16 0' l 40'1 Ca ppm .318 Mg ppm.093 Na ppm .093 K ppT 340 Zn ppm.132 Mn ppm .2 Fe ppm .835 Cu ppm .202 Pb ppm .*015 JTU 13.3 Mg/i dry wt. 16.*06 Sr ppm .0013 *386 *147 ,085 .400 .104 .129 .941 194 023 190 22.38 ,o225 o167 .090 .072 ,071 .057 .245 .210 .03 *046 .110 .100 .787 -.627 .119 .100 .016 .014 12.5 16.5 15*. 17 19.61 ,0016 .0025 .0009 .003 Depth *335 .171 080 .330 604 * 164 .122 .015 20.0 23.49 * 093 *043 .222 *390 .129 .057 .574 o140 8. 6 10.o85 .092 .039 131 .372 *098 * 087 .5.26 .123 10.9: 13.40 PJ1+1 ~r~m 1%7 . 1%Y _I 1() _I~)~) 107 Tabl e 15 Averaged chemical element composition, of suspended matter. collect-ed. August 9 and September 20, 1967 between Columbus, Georgia land river mile 120 Depth Ca ppm Mg ppm Na ppm K ppm Zn ppm Mn ppm Fe ppm Cu ppm Pb ppm Cr ppm Ni ppm Co ppm Cd ppm JTU Mg/1 dry wt. Sr ppm 0' s292 .116 .075 .283 .076 .,133 o788 o130 018 13.0 15.73 o-0014 20' .306 .138 088 .337 080 .140, 9763 e136 .017 16.1 19.16 *.0017 401 *319 S170 .077 .405 024 .159 o 950 .095 ,012 1900 22.038 s0021 Segut 20 0f 1 *2'21 .068 .415 .134 .029 o573 .052 .016 .032 ,006 .0009 .0009 7.5 9.63 .0013 108 Table 1.6 Averaged chemical element composition of suspended matter collected on August 29, 1967 between river mile 98 and Walter F. George Da' Depth O' 20' 40' 60' Ca ppm .195 .197 .213 .205 Mg ppm .014 .014 .020 .019 Na ppm .079 .083 .085 .081 K ppm .226 .236 .220 .185 Zn ppm .120 .126 .105 .097 Mn ppm .020 .035 .074 .185 Fe ppm .337 .225 .316 .443 Cu ppm .146 .150 .159 .146 Pb ppm .0016 .0018 .001 .002 Cr ppm .0077 .0025 .004 .0095 Co ppm .0001 .0003 .0017 .0005 JTU 7.33 9.0 10.7 11.75 Mg/l dry wt. 9.44 11.30 13.18 14.34 Sr ppm .0001 .0001 .0001 .0001 109 Table 17 Averaged chemical e lement composition of suspended matter collected on August 16 and 29, 1967 from tributary creeks on Lake Eufaula Dep th Ca ppm Mg ppm Na ppm K ppm Zn ppm Mn ppm Fe ppm, Cu ppm Pb pp m Cr ppm .Co ppm JTU Mg /I dry wt. Sr ppm August 16 0' .251 o080 .098 .026 .036, o168 .128 9257 .300 .124 .149 .03 6 .057 .349 .601 .161 .105 7.5 9.63 15.3 18,28 August 29 0' 25' o177. .306 .014 .043. .092 .087 273 .253, 0092 .103 .018 .134 .130 1.390 .159 .140 003 .005. .022 .028 .0005 00001 4.2 .280 5.98 32.35 .0002 .0001 ~yrw; -- r( V( .L 110 In addition to the reduction in Ca content, there was a com- parable decrease in Mg and Fe content and a lesser decrease in Mn and K content :in August. All of these elements varied concurrently in an apparrently related manner., In contrast, the Cu content remained fairly consistent both in time and in location within the suspended matter from main reservoir. Zinc concentrations increased with time and in location. It is not understood exactly what is the source or, more importantly, the significance of what appears to be a relatively high concentration of Cu and Zn in the suspended matter from this reservoir. An examination of elemental content of suspended matter from tributary creeks indicates a greater degree of chemical variation between samples of surface and bottom waters than was evident in main reservoir during 1967. This difference was attributed to more stratified condition within creeks in 1967 than was evidenced in main reservoir. In all of these suspended matter samples there was a detectable amount (generally above 10 ppb) of Pb and Cr. In those samples from main reservoir the Pb content appeared to be greater, whereas in the tributary creeks the Cr content was higher. Neither the source nor significance of these two elements are understood. While the discussion of these data has been limited, this is an area of research that has here-to-fore been ignored but is a most important aspect of reservoir water chemistry. Needless to say, much effort will be expended during next two years to develop and refine techniques and to accumulate sufficient data to gain some 111 insight into the role of these chemicals in the suspended matter and particularly in attempting to separate the colloidal, dead and living suspended matter. Light penetration , which is a physical factor dependent upon the degree of water turbidity, was measured at irregular intervals but under sufficiently different water conditions to give on under- standing of the variations of light intensities within these surface waters. These data are presented as foot-candles of surface illumi- nation, and as foot-condles and percentage of surface illumination for the various water depths, in Table 18. 112 Table 18 Foot-candles of illumination at surface and at various water depths in Lake Eufaula, with corresponding percentage values of surface light concentrations at the given depths, and including turbidity values, in parenthesis, under appropriate water depths for specific locations and dates indicated Location river Turbidity Foot-candles light/percent surface illumination at various depths mile Date (1) 0' 1' 2.5' 5' 7.5' 10' 138 7-20-65 8400 2239/26.6 46/0.5 2/.002 (N) (19) (53) 129 7-20-65 10000 5577/55.8 236/2.4 43/.4 (N) (40) (36) 117 8-3-65 10200 4293/42.1 1431/14.0 751/7.4 107/1.0 117 11-4-65 7400 3065/41.4 634/8.6 148/2.0 5/0.7 (N) (14) (11) 116 7-20-65 9200 4963/53.9 2057/22.3 460/5.0 (N) (33) (35) 112 7-20-65 10600 5643/53.2 275/2.6 22/.2 (N) (34) (31) 112 8-3-65 9800 6149/62.7 1537/15.7 154/1.6 61/.6 96 8-3-65 9150 3176/34.7 508/5.6 57.6 90 7-23-65 5200 2696/51.8 866/16.6 385/7.4 (N) (16) (15) 96 10-4-66 5900 3747/63.5 1648/27.9 607/10.3 34/16 (JTU) (8) 75 8-23-66 2000 1666/83.8 666/33.3 267/13.3 27/1.3 (7) 75 10-4-66 2000 1866/62.2 733/24.4 53/1.8 130 6-15-67 6800 4482/65.9 2627/38.6 309/4.5 (JTU) (14) 119(Cr.) 6-15-67 9150 5363/58.6 4732/51.7 1262/13.8 883/9.7 (JTU) (7) 116(Cr.) 6-15-67 5700 1350/23.7 600/10.5 144/2.5 24/.4 (JTU) (9) 111(Cr.) 4-19-67 8200 3360/41.0 1210/14.8 457/5.6 168/2.0 108 4-19-67 6750 2825/41.9 1614/23.9 461/6.8 184/2.7 107(Cr.) 4-19-67 6800 3920/57.6 2248/33.1 761/11.2 323/4.7 10? 4-19-67 5800 2213/38.2 843/14.5 242/4.2 74/1.3 95(Cr. ) 3-29-67 6000 1789/29.8 488/8.1 A55/7.6 95(Cr. ) 8-29-67 3100 1500/48.4 391/17.6 195/6.3 49/1.6 (JTUJ) ( 5) 96 0-29-67 5300 2650 50.r0 4 4/8.2 72'1.4 (JTU) (16) 86 P-29-67 6700 4982/74.4 3092/46.1 1546/23.1 481/7.2 69/1.0 (JTU) (4) 1. (N) = Nephio values for turbidity 113 Discussion of Water Composition Data It is evident from previous sections that during the course of this research considerable effort has been exerted to obtain more reliable estimates of the parameters under study by improving old techniques and by developing or by utilizing new techniques. As a result it is believed that the estimates obtained for each successive year are more nearly representative than those for pre- ceeding years. On a drainage area as large and complex as the one for Lake Eufaula, many factors contributed to the quality of the impounded waters. Some were man-made factors, such as domestic and industrial pollution; others were combinations of man's activities coupled with natures, such as soil erosion; and others were natural factors, such as seasons, temperature, and rainfall. When all of these became interactive, a wide variety of water quality conditions could and did exist. It would be impossible to completely catergorize causes and effects on water quality conditions. Rather, on attempt will be made to show the interdependence of measured water quality conditions during this study period. Turbidity, which is a relative measure of the quantity of sus- pended matter in water, has been measured on Chattahoochee river at various points in Georgia, since early 1900's. In the early 30's these waters often contained over 400 ppm (JTU) of suspended soil particles and colloids.(1) (1) Albert, Frank A., and Albert H. Spector. 1955. A new song on the muddy Chattahoochee. Water, The Yearbook of Agriculture, USDA, U.S. Government Printing Office, pp. 205-210. 114 This was largely the result of row-crop farming of the hilly redland portions of this drainage area. During the course of this present study, waters collected from this general region on the Chattahoochee river never exceeded 67 ppm (JTU). This reduction has occurred largely as a result of farm land being taken out of cultivation and used as permanant pastures or planted in pine trees. Within the lake itself the upper third is mainly a deep river- run area and the middle third is the shallower (upper) inundated area. These two regions of the reservoir serve primarily as the settling basin allowing the lower third of lake to remain clear a majority of the year. Under clear water conditions the turbidity generally ranged from 4 JTU's near the dam to 16 JTU's in river at Columbus. Most of this suspended matter was a mixture of living and dead phytoplankton plus other organic debris. Since the higher turbidity values (20+ JTU's) resulted largely from suspended soil particles transported by surface runoff, the quantity of suspended matter was dependent upon season of the year and duration and intensity of rainfall (locally it might also have been dependent upon construction and mining operations on the water- shed). While these muddy waters (20-60 JTU's) contained considerable detectable Fe (.5 to 1 ppm), a more moderate amount of turbidity (15 to 20 JTU's) likewise had an equivalent Fe content. It is sus- pected that much of this moderate turbidity resulted from suspended Fe eolloids. Under these same conditions, the detectable concentrations of Mn was lower in muddy waters and higher in the moderately turbid waters. 115 Turbidity may also be used to measure the quantity of organic matter in form of phytoplankton in clear lake waters. The removal and analyses of the suspended matter would provide on approximate estimate of its chemical composition. Likewise, on analysis of the filtrate (water) would shed light upon those elements which were in such small particles as to pass an 8 u filter or were in solution. While data on suspended matter are limited, they offer some trends in composition which will be pointed out below. Generally, in Lake Eufaula waters, turbidity assumed to have been associated with phytoplankton growths never exceeded 16 JTU's and in a majority of cases had a value of 10 JTU's or less. This in itself indicates a low order of microscopic plant growth since fertilized ponds may often exceed 16 JTU's of turbidity in their surface phytoplankton growths. The averaged chemical composition of surface water samples of phytoplankton, and associated suspended matter, and filtrates from these samples from each region of the reservoir, and from a farm pond and from plastic pools are given in Table 19. A comparison of the JTU values from each location indicates some degree of difference in quantities of suspended matter present in each area, but when a comparison is made of the chemical composi- tion of suspended matter and filtrate there is not an obvious correlation between the two sets of data. These date, which are probably the most comprehensive sets of information on this par- ticular phase of reservoir water chemistry available to-date, pose more questions than answers at present. 0\ Tbl1e 19 Compar ative-chemical compositions of suspended matter and filtrate water of samplescletdfo various portions of Lake Eufaula and a fertilized fish pond mid portion August s~.f.H 2 0 8.6 .093 2.990 .043 1.242 .574 .057 .006 *140 .007 .129 .017 .221 6.120 .390. 1.*550 0 001 lower portion August Region Date Sample JTU Ca Mg Fe Mn Cu Zn Na K Pb Cr 202 3.000 1.175 050 .012 030 .037 49975 1.375' L. Eufaulad upper portion September Lsome 3s .m. 7.65 1.223 .057 .448 .022- 048 *127 e215 .457 .016 0030 2.500 .850 087 .016 10.775 1*200 S-6 September sOm. f HO2 3.9 .085 3.000 .020 1.970 .060 .100 .039 .015 .0316 .015, .040 .035 .053 1.400 .300 .800 .002 .070 creeks August 16. some f H 0 7.4 083 .029 .354 035 .155 .172 .271 3.22 1.09 .006 .010 *oil 4o220 1.380 Lo Eufaula Creeks... A ugust 29 4.-2 .177 130 *018 .159 .092 .092* *272 003 2.900 243 *005 006 5.810 1.360 Co .0001 01 0 015 sOm. 3.0 187 *008 265 .016 .135 o.130' .078 .230 002 010 .001 001 015,0 117 It has been known for a long time that species of phytopiLnkton have pulses of growth, as far as population numbers and ages of individual cells are concerned, but the chemical composition of these pulses are unknown. From more extensive sampling of phytoplankton growths in fed fish ponds, data have been obtained which indicate some degree of chemical element cycling in ponds, but also suggest that the quantities of such elements may decrease with advancement of season while population numbers may increase (Figures 16 and 17). This same phenomenon was also indicated by a decline in chemical element composition of suspended matter collected from Lake Eufaula waters on 4 successive sampling dates in August 1967 (Figure 17). Thus, our present state of understanding can be summarized by saying that the technique devised to study suspended matter in surface waters has yielded variable data that suggest seasonal trends. However, until more sophisticated equipment is available to separate living and dead phytoplankton and suspended colloids in these residue samples, a complete understanding of even the cyclic nature of these data will be impossible. An interesting feature of all data on residue and filtrate chemical composition has been that the Ca and Mg contents in raw waters have consistently been less than the total quantities calcula- ted from residue + filtrate content. In the case of metallic elements, the accountability of raw water content to residue + filtrate con- tent has been rather good. Light penetration data indicated a sufficient quantity of light within the upper 7 feet of water to support plant life. From prior POND 6 0 TURBIDITY 60.VARBON PPM PPM 401 40- S-1 201 20 / A 8CODE A 8-CD E 60- 60- 40- 40- S-7. 0 0 S-I1I 4 0 20 0. CALCIUM 6 MAGNESIUM 6-IRON 41 22 01 00 >-r A 8CD0E A cD 4 2 0 2 l 6 4 4 S-12 Figure 16. Relative abundance and chemical composition of suspended matt Ier (shaded area) and filtered water (clear area under shaded area), expressed as ppm concentrations in original surface water samples collected from 4 ponds (which received-reguladr applications-of organic fish feed) on June 28 (A),*July 25 (B), August 21 (C), September 1 (D), and October 3 (E). N co ZINC 0 / 6 4- 0A 0 A , C - r6 a" 2 0 b D-r rAl; : -~:t.~ ,I I(ifS ,I ii . 1 , I 30 TURBIDITY .20-1 0' 15- CARBON 10 6 4. 0. CALCIUM I" A 4 ,'5 MAGNESIUM IRON B.B5. b MANGNESE .2 0, -a t- 0D 6 .soD 4 2 0 D POTASSIUM o. 0 .1* .3.COPPER __ BCD ZINC .2 4. 4 2. 0 B BC D AB8 CD AB B C D 10 15 663.33 ;10114-4- 2... 0: 22 2 .12 0 0 0. 0 000 o ui C D u Figure 17. Relative abundance and chemical composition of suspended matter (shaded area) andfled water (clear area un<-.,r shaded area), expressed as ppm concentrations in, original ae samples collected at specified locations and depthLs of Lake Eufaula on August 3 () August 9- region 1 (B), August 9- region 2 (C), August 16 (D), and AugustL 29 (E). RIVER 0' RIVER 0'-60' 30- 200 10- S-, o,' T~b CREEKS 0! B0 BC .3- 1' - - - B B CREEKS 30+ IH 4_, aE .'4 t= . 0A ol A 5 8 C D 120 1 research by Blackburn at this Station, it was determined that certain submersed rooted plants thrived on light intensities as low as 10 foot-candles. Other data obtained here by Beasley on light penetra- tion into a heavy growth of Microcystis sp. indicated that photosyn- thetic action occurred at approximately 5 foot-candles of light in- tensity. In water, a 50% higher concentration of Ca was present in samples collected in early spring than was evident in those collected in summer and fall. On the otherhand, Na, K, Cu, Zn, and P concentra- tions in these same water samples was lower during spring period than in summer and fall periods. The Ca-Mg pattern within Lake Eufaula during the course of this study can be summarized by stating that the averaged relationship varied from 2.43:1 to 4.44:1. The Fe-Mn patterns in Lake Eufaula waters during period of stratification and immediately following an overturn are illustra- ted by following data. Condition Element concentration ppm Stratified raw H 2 0 filtered H 2 0 D. O> 1 Fe .046 .016 Mn .017 .003 D .01I Fe 1.145 .621 Mn .452 .108 Blackburn, R.D. The effects of various light intensities and light sources on the growth of Elodea densa (Planch) Caspary and Heteranthera dubia (Jacquin) Macmillian. M.S. Thesis, Auburn Univ, 83 pp. 1959. 2 Beasley, P. G. The penetration of light and the concentration of dissolved oxygen in fertilized pond waters infested with Microcystis. M.S. Thesis, Auburn Univ., 70 pp. 1962. 121 Condition Element concentration ppm following overturn raw H20 filered H 2 0 D.O.>1 Fe .119 .017 Mn .137 .004 D.0 <1 Fe .926 .600 Mn .537 .557 A curious feature of these data is concerned with percentage- remaining-after-filtration ratios between Fe and Mn in stratified waters (ratio approximately 2:1) and in overturned waters (ratio approximately 1:2). This is a partial explanation of why the Fe- Mn ratios for 1965 and 1966, when there were numerous periods of stratification with complete D.O. depletion, were lower than in 1967 when D.O. was present even in the deeper waters throughout the reservoir. Occurrences of minor element constituents in Lake Eufaula waters during early spring months were detected by condensation of river water, dissolving the suspended matter and analyzing the en- tire resulting solution. Averaged concentrations of those elements checked were as follows: Sr 0.0011 ppm Ni 0.0136 Cr. 0.0517 Cd 0.0007 Co 0.0010 Pb 0.0079 Averaged concentrations of same minor element constituents in raw waters from Lake Eufaula during summer months were as follows: 122 range Sr 0.0082 ppm .001-.03 Ni 0.0210 .01 -.03 Cr 0.0146 .001-.03 Cd - Co 0.0036 .001-.005 Pb 0. 0070 .001-.04 The concentrations of these same minor elements in tributary creek waters of Lake Eufaula were the same as given above for all elements except Sr which was 0.0181 ppm. The dynamics of physical characteristics of the waters in Lake Eufaula throughout this 2-1/2 year study period can be further emphasized by presenting the averages for inflowing and outflowing waters and minimum and maximum values obtained on each characteris- tic that was measured within the lake. These data are presented in Table 20. In Table 21 the chemical composition data have been applied to averaged inflow and outflow data and the approximate quantities of each element entering upper region of Lake Eufaula, the quantities passing through lower region, and the quantities leaving the reservoir in tailwaters for each 24 hour period are given. The gain or loss column gives some indication of those elements which are retdined in bottom muds and those which are flushed from the reservoir. In the case of calcium, it has been observed that concentrations in tailwaters were often higher than in bottom waters of reservoir immediately above dam. River banks and relief wells (both high in Ca) immediately below turbine flumes possibly account for this slight increase in Ca concentrations in tailwaters. The most significant contribution derived from these gain and loss 123 Table 20 Averaged inflow and outflow. composition of Lake Eufaula waters in-'" cluding 3-year range in lake water composition pH 3 Ohms./cm Turbidity, JTU's Alkalinity, ppm CaCO EDTA hard, ppm CaCO Ca ppm Mg Na K Zn Cu Fe Mn N p CT .C gamma counts/mmn.( Cl 2 SO 4 Inf low water 6.96 16761 18.25 2000 14.62 4.16 1.17 5.37 1.45 043 .015 .472 .058 ,208 044 11.73 5.43 (1)Background gamma counts ranged from 549-980 counts per mmn. .... in lake 5.*5-9*. 11,700-22,000 1.7-68.0 6. 6-49. 7 11.5-40.0 .51-14.0 .50-2.07 1.5-12.5 .01-3.5 ,001-1. 19 *001-.63 .001-1,25 *001-,05 .01-1.92 .001-,.21 3 .6-23 .5 2.5-12.0 273-W486 1.0-1500 3.5-10.0 water 7,13 16171 11.37 22.07 19.5 5.,22 14.19 3.*89 1.*40 .031 .012 .478 .040 .1.33 .029 10,08 6.92 5.05 5,50 124 Table 21 Calculated average pounds per-day for 3 year period of elements entering upper region, passing through lower region, and eliminated through tailwater, with indicated gain to or loss from reservoir':each day I nf low Upper Region 10,9351 lbs/day 243,576 6 8,505 108,321 2,517 878 27,636 12,178 2,576 686,815 317,937 Lower Region 10,900 lbs/day 257,628 73,190 305,641 95,439 4,508 2,166 16,218 7,787 14,403 1,873 695,012 275,779 Outf low Tailwater 101870 303,203 69,121 225,950 81,f319 1,800, 697 27,764 2,03 23 7,If725, 1,684' 585,496, 401,948 Gain or loss() within reservoir Inflow-outflow lbs/day 59,f62 7 - 616 88,474 27,002 717 181 128 .1,073 4,453 .892 101,3 19' .84,1011. 17,038 Ca Mg Na K Zn Cu Fe Mn N p C T CC. 2 C S0 4 1 ppm 58,5525, Flow CFS 293 ,3 29 319,467 . ..... - ~--- 58,085 125 data is the increased confidence which can be placed on the analyti- cal data on whibh these computations are based. During the early 1900's some chemical analyses of waters collected from the Chattahoochee river near West Point, Georgia were made and reported by U.S. Geological Survey. These data are summarized in Table 22. In summarizing the chemical composition of rivers of the eastern and gulf region of the United States, Clarke (1924) states (p. 79) ---"All are low in salinity and relatively high in silica and alkalies. In several of the analyses the alkaline radicals are in excess of calcium. River waters, in short, seem to exhibit distinct regional peculiarities, which, in most cases, if not in all, are due to the geology of the region transversed. These waters with one or two exceptions, flow from areas of crystalline schists, and owe little to sedimentary environments." This statement is in agreement with data accumulated by this study. A more recent (1959) analyses of waters from the same river system was made by this same agency, and these results are summarized in Table 23. In concluding this discussion on water composition in Lake Eufaula, it is evident that urbanization and industrial develop- ment on this river during the past half-century have had a limited influence on many of its chemical constituents. 126 Table 22 Averaged analyses of 34 composit6d water samples collected from Chattahoochee rive 1 at West Point, Georgia between October, 1906 and October, 1907 CO 21.32 ppm 3 SO 4 8.49 ppm C1 3.96 ppm NO 3 1.32 ppm Ca 9.06 ppm Mg 1.51 ppm Na 12.08 ppm K 3.40 ppm S&0O2 37.73 ppm Fe20 3 1.13 ppm Salinity 52.00 ppm (1) Source: Clarke, Frank W. The data of geochemistry. USGS Bul. 770, 5th Ed. 1924, pp. 78-79. Table 23 Minimum and maximum concentrations of elements, ad determined by spectrographic analys in Apalachicola river waters collected at Blountstown, Florida. ppb "058 .11 73. 25 50 5 -11 21 -42 .058 ,75 2.2 am 7.8 2.1 -51. 96 -1220 .075 -. 12 4 -25 0 - 62 2.6 -34 0 -58 2.1 -6.2 .75 - 2.1 1.3 7.5 -34. .8 - 99 0 - 2.2 (1) See Appendi.x Table 8 From : Durum, W. H. Ag Al B Ba Be Co Cr Cu Fe Li Mn Mo Ni Pb Rb Sn Sr Ti V Y I L-- III III 1 I I11 lein 128 Chemical Characteristics of Bottom Soils The soils covering the bottom of Lake Eufaula are sedimentary types since the area inundated was river flood plains. The physical composition of these bottom soils varied from almost pure deposits of sand, to sandy loams, to varying colloidal mixtures of clay and organic matter. The location, thickness, and area covered by each of these deposits appeared to be almost completely dependent upon conditions existing prior to flooding of the area. For example, in the main river channel, large sand bars were still in existence in 1967 throughout the entire length of the impoundment. Whether or not these sand bars are shifting is unknown, but sampling of these areas revealed an absence of silt deposits on their surface. A somewhat similar condition existed on sand bars located in shallower water areas. In these cases, the sand bars apparently formed slight ridges on the lake bottom-and silt deposits were apparently collecting in the troughs between these sand ridges. Such a situation is be- lieved to be the result of silt shifting by bottom water currents. When bottom soil sampling was initiated in 1965, the existence of the extensive sand bars in the old river channel restricted core sampling to those shallower flooded areas where sufficient clay existed to permit a core sampler to be withdrawm from the lake bottom. Consequently, much time and effort was expended in bottom soil sampling. However, a series of representative samples from various areas in the upper and middle portion of the lake were obtained, and data on their chemical composition are given in Table 24. 129 Table 24 Quantities (average and range) of chemical elements recovered from neutral cation exchange extractions of 1965 cored soil samples from 10 to 20-foot depths in Lake Eufaula Ca ppm 1 ) Mg ppm Na ppm K ppm Sr" ppm Zn ppm Mn ppm Fe ppm Cu ppm Pb ppm Cr ppm Ni ppm Mo ppm Co ppm Cd ppm C % P ppm Ave rage 1354.04 153.63 23,037 69*921 5.331 8.216 111.26 6.126 2.80 3.858 1,316 .384 *679 * 073 *0758 1.255 1*015 Range 216 - 2088 50 - 301 4- 60 28 - 116 2.4- 11 2 - 17.2 40 - 224 4.2 - 11.2 1.9 - 3.2 2.0 - 9.4 0.01 -2.5 0.1 - 0.8 0.1 - 3.0 0.2 - 0.5 0.05 - 0.12 0,031 - 0,102 0.96 - 1.75 0.4 -2.4 ()PPM pig/g dry weight of soil. ru v()vvv 130 During 1966 the same core sampling technique was employed. While much time and effort had to be expended to obtain these samples, a greater degree of successful sampling was possible through the use of a depth indicator to locate the more silt-laden bottom areas. As a result, core samples of sufficient thickness were available to permit their separation into an A (top 1" of core) and B (lower 4+" section of core) horizon. Prior to separation into the 2 horizons, these core samples were allowed to air-dry within the original sample tube. Thus, the associated water collected with the core was allowed to evaporate and the soluble contents were retained in the soil sample. The data on the chemical composition of horizons A and B of soil samples collected in 1966 are summarized in Table 25. During the winter draw-down period from January to March, 1967 an extensive series of soil core samples was collected from the dewatered bottom at an elevation of 4' to 5' below normal pool level. This was on important series of samples since they were taken within that bottom area which is the potential habitat for rooted submersed and emersed aquatic weeds. The thickness of this series of core samples was uniformly between 31 and 4", thus no attempt was made to divide these samples into an A and B horizon. This decision was also influenced by the fact that this sampling area was a region subject to current as well as surface erosion and no surface silt deposits were evident when the samples were collected. Data on the chemical composition of this series of soil samples are given in Table 26. As a result of the difficulties encountered in using the soil 131 Table 25 Quantities (averages and ranges) of chemical elements recovered from neutral exchange extractions of 1966 cored soil-samples from.-2.. to 20-foot depths in Lake Eufaula Horizon Ca ppm Mg ppm Na ppm K ppm Sr ppm Zn ppm Mn ppm Fe ppm Cu ppm Pb ppm Cr ppm Ni ppm Mo ppm Co ppm Cd ppm N % c % P ppm Averag 528.6 102.29 18.93 54.81 3.96 16.236 122.81 19.63 2.73 4.14 .663 1.0263 2.587 .557 .233 .0533 1*128 2.175 13 Range Average 88.0 - 869.0 701.09 18.7 - 196.9 130.24 9.3 -36.3 19.39 8.4 90.0 65.77 1.0o 5.28 3.68 2.7 153.0 24.464 17.7 - 379.5 .131.11 4,7 - 30.0 9.22 11 8.3 4.09 .8'- 9.5 2.74 .3 01. 904 .3 4.5 11 .3- 12.0 2,782 .2 -1.10 .518 .06 - 85* .331 .011 * 095 .0563 .41 - 2.07 1.120 '99 - 3.15 2*515 (1) PPM jig/g dry weight of soil. Range 133 - 1353 58.5 -220 6.9'- 37.3 18.0 - 132.,0 0.9 - 12.3 2.4 - 180.0 27.5 - 220.0 5.0 - 14.0 1.4 - 10.5 *4 - 12.0 .45 - 1.5 o3 - 2.5 *3 - 8.4 .10 -190 .15 vim.74 .031 077 .52 1.77 1.21 -6.30 132 Table 26 Quantities (average and range) of chemical elements recovered from neutral cation exchange extractions of 1967 cored soil samples from- dewater edge (4- to 5-foot depths) of Lake Eufaula Average 652.5 102.06 13*075 43.896 2.525 14.663 83.742 10.715 5.23.3 2*725 .872 1.113 1.690 .535 .446- .0606 .891 1*925 Range- 45 - 2560 9.0 - 195.9 468 - 28.6 6.0 - 16000 .25-9.68 1.5 -132.0 2.0 -440.0 3.5 -45.0 1.4 -15.5 *2 -20.0 ,05 -2.'8 *4 230 .1-9.2 .1 3.0 .1 -1.3 .003 - 260 .12 -3.03 99-3.75 (1) PPM= pg/g dry weight of soil. Ca .ppm Mg PPM Na ppm K ppm Sr ppm Zn ppm Mn ppm Fe ppm Cu ppm Pb ppm Cr ppm Ni ppm Mo ppm Co ppm Cd ppm N % P ppm ~~ TT~m 133 core sampling apparatus, a new bottom soil (hydrosol) sampler was designed and built by the Project Leader in 1967. This sampler has already been described in the section SAMPLING EQUIPMENT AND PROCEDURES of this Report. A sampler that would consistently collect representative samples of bottom materials existing within the so- called interface area between water and bottom soil has long been needed. It has been suspected that this area is a rich reservoir of precipitated organic and inorganic matter that may, under certain conditions, be in constant exchange with the water. Other types of bottom samplers capable of collecting such a sample have been so small in cross section that they disturbed and dissipated the hydro- sol to such an extent that an inaccurate sample was entrapped in the sampler. After the sample;was entrapped, all substrate conditions had to be specific, otherwise the sample could not be retrieved by the sampling apparatus. The hydrosol sampler has many advantages. Firstly, it was light in weight and could be operated by hand if necessary. Secondly, it could be operated at any water depths and would retrieve the hydrosol sample with equal effectiveness from any depth. Thirdly, it would collect the fluid fraction over any type of bottom substrata, but was more effective over a muck bottom. Forthly, samples collected by this sampler have contained a much greater concentration of exchangable elements than have those collected with other devises. This last statement is illustrated by the data in Tables 27 and 28 on chemical composition of hydrosols collected from main reservoir 1 34 Table 27 Quantities (average and range) of chemical elements recovered from neutral cation-exchange extractions of 1967 hydrosol samples from 3- to 80-foot depths in Lake Eufaula. Ca ppm Mg ppm Na ppm K ppm Sr ppm Zn ppma Mn ppm Fe ppm Cu ppm Pb ppm, Cr ppm Ni ppm Mo ppm Co ppm Cd ppm N% P ppm 1641.1 378.2 379.4 182.7 4.73 28.31 539.4 322. 8.17 3.58 3.*29 1.98 2.67 .79 o1965 2.343 48.91 (1) PPM pg/g dry weight of soil. 775,.3250 190-2150 38-1950 50-730 e75-20 6.5-90 80-1330 11-3950 .2-30 .3-18 .2-45 .35-7.5 .1-45 .14-10 o0735-*552 .780-3.322 2.1-360 135 Table 28 Quantities (average and range) of chemical elements recovered from neutral cation exchange extractions of 1967 hydrosol samples fromi 8*0 to 50-foot depths in tributary creeks of Lake Eufaula Average 1628.5 266.085 188.15 154.0 3.815 19.05 321.85 167.15 8.83 6.00 2.145 1.720 1.356 .3895 .1949 2.556 89.98 Rang.e 370-2880 50-555 30-540 60-240 1-10 4.3-48 105-545 8-1000 .5-17 .3-16 .5-10 .4-8.6 .18 -4.3 o07-*86 .0112-,.3421 .*683-4.153 2.1-240 )PPM = pg/g dry weightof soil. Ca' ppm Mg ppm Na ppm K ppm Sr ppm Zn ppm Mn ppm Fe ppm Cu ppm Pb, ppm Cr ppm N i ppm Mo ppm Co ppm Cd ppm N % P ppm 136 and tributary creeks of Lake Eufaula in 1967. Comparative data on extractable elements in core and hydrosol samples collected from various areas of Lake Seminole during this same period are summarized in Table 29. Additional data on hydrosol in an upstream impoundment, Bartlett's Ferry Reservoir, are summarized in Table 30. The chemical composition data on bottom soils presented in each of preceeding Tables represent those quantities of elements which can be removed or replaced on the soil colloid by a neutral cation exchange reaction. These data do not represent the chemical composi- tion of these soils. Rather, this is the best technique available to estimate those quantities of elements which might become available for use by various forms of aquatic plants. In each of these tables (Lake Eufaula data) the averaged quantity of each element exchanged from the soil samples are given followed by the minimum and maximum quantities removed from samples in each series. It will be noted that most averages are approximate mid- value of the ranges given, indicating that sampling was of a rather random nature and that no particular evidence of biased values is present. Thus, we can assume that these values are representative of exchangable chemical quantities in the soils from those areas of Lake Eufoula that are represented in these sampling data. In evaluating these data on exchangable elements from bottom soils of Lake Eufaula it is evident that sampling technique was a major factor in determining the quantity of an element or elements that could be recovered from a particular sample. In most cases 137 Table 29 Averaged composition of bottom soils, collected by 2 methods, in various areas of Lake Seminole during 1965, 1966, and 1967 :,f /I/ I Hydrosol Hydrosol Hydrosol Hydrosol Core Hydrosol Core Core Core Hydrosol Co ppm 1900 3350 2781 4786 455 2804 532 562 595 910 Mg ppm 250 113 45.3 51.9 15.8 64 6.6 31.1 30 28 Na 135 508 109 78 9 237 9.3 35.7 8.1 100 K 150 153 66.7 140 46.2 86.7 45.7 92.5 20.2 40 Sr 2.5 1.7 1.1 1.52 .61 1.72 .6 - .97 .5 Zn 25 10.6 21.8 19.6 3.2 16.3 2.25 .7 2.85 4 Mn 644 232 423 254 57.7 658 127.5 37.3 74 237 Fe 14 59.5 60.3 107.3 10 128 9.35 72.8 8 40 Cu 6.5 13.8 5.3 9.13 4.54 6.78 4.9 .37 5.75 14 Pb .6 11.6 .47 3.13 .64 1.6 .8 1 1.2 Cr 2 2.75 1.67 1.53 1.18 1.08 .4 1.5 .5 Ni .3 1.2 .58 1.13 .8 1.67 .6 .8 .2 Mo 2.2 1.56 1.8 .65 Co 3 .95 2.28 2.09 .3 .56 .2 .65 .25 Cd .57 .80 .41 .35 .67 .37 .2 .37 1.0 N% .233 .268 .283 .3557 .268 .345 .339 .091 .373 C% 3.06 9.882 2.60 5.756 7.18 6.09 .923 1.09 5.59 P ppm 6.9 12.77 27.10 32.2 1.68 30.9 1.26 7.62 2.20 4.20 138 Table 30 Quantities (average and range) of chemical elements re Icovere d from. neutral cation. exchange. extractions of 1967 hydrosol samples from 10.. 40-foot depths in Bartlett's Ferry Reservoir, Ca ppm Na ppm K ppm Sr ppm Zn ppm Mn ppm Fe ppm Cu PPM Pb ppm Cr ppm Ni ppm Mo ppm Co ppm Cd ppm N % P ppm 964.0 195.2 176.6 18200 2.79 14.10 305.6 251.5 12.0 1.*40 2.54 1.52 1. 11 .734 .278 2.146 5.84 (1) PPM = j'g/g dry weight of soil. Range. 780-1340 125,-240 155- 230 120- 280 8.0-22.0 210-470 28-830 1.5-18.0 .25-2.00 010-8.5 .50-4.0 .65-2.0 .40-1.0 *163-o550 1.92-2.41 4.2-10.0 Wk A~rrr I n~ 139 the averaged quantity of an element 2ecovered from any hydrosol sample exceeded the maximum quantity of that element recovered from any core sample. However, this does not indicate that all necessary data on soil composition studies in a reservoir could or should be obtained with a hydrosol sampler. For example, the marginal sampling can only be accomplished with a core sampler if one is to obtain reliable data on elements available to plants whose roots extend several inches beneath the soil surface. Likewise, one should use the hydrosol sampler to determine those exchangable elements that could be utilized by various forms of algae and floating plants. Since the specific applications of these data on exchangable element from soil to growth of aquatic plants is unknown at present, it will suffice to summarize this discussion at this point in the report with 2 statements. First, with a few exceptions the quantities of each exchangable element recovered was 2 or more times greater in hydrosol samples than in core samples. Other comparative data on quantities of exchangable elements in rich and poor aquatic soils are given in Tables 31 and 32 and 33. It is quite evident from these data that the geological formations associated with a particular drainage basin have a profound influence on quantities of exchangable elements present in inundated aquatic habitats. Enhancement of these quantities by man's activities within a given basin is also evident. 140 Table 31 Averaged quantities of chemical elements recovered by neutral cation exchange extraction of bottom soil samples from Wapanocca Refuge Lake in Arkansas Ca ppm 8275.4 Mg ppm 578.5 Na ppm 18.289 K ppm 191.51 Sr ppm 13.67 Zn ppm 26.27 Mn ppm 429.5 Fe ppm 59.67 Cu ppm 6.175 Pb ppm 48.68 Cr ppm 3.466 Ni ppm .705 Mo ppm .532 Co ppm .599 N .424 C % 4.260 P ppm 3.034 (1) PPM = pg/g dry weight of soil. 141 Table 32 Averaged quantities of chemical elements recovered by cation exchange extraction of samples collected from surface of soils in 'W' series plastic pools (1965), by core sampling in numbered series (1966), by hydrosol sampling of same numbered pools 1 in 1967 1965 1966 1967 Ca ppm 417.33 1940. 271.57 Mg ppm 107.48 287.5 59.94 Na ppm 24.93 332.5 48.65 K ppm 84.05 170.0 76.214 Sr ppm 3.756 2.52 3.014 Zn ppm 23.39 18.37 70.98 Mn ppm 130.71 401.0 49.71 Fe ppm 11.025 184.0 14.657 Cu ppm 2.508 14.0 6.742 Pb ppm 4.566 1.42 7.500 Cr ppm .740 .72 .571 Ni ppm 1.025 1.47 .928 Mo ppm 2.383 3.028 Co ppm .550 1.137 .550 Cd ppm .143 .955 .100 N % .2054 1.053 C % 7.625 P ppm 6.560 5.43 2.196 (1) Pool Nos. 18, 23, 37, 38. 142 Table 33 Averaged quantities of chemical elements recovered by 'neutral cation exchange extractions from soils in numbereld 1 and lettered 2 plastic' pools in. 1965 Numbered series 47000 47.25 58.50 145.0 17 83.12 76.25 .51 .053 . 693 5.25 4*0 29 Letter series 355.0 29.5 48 *0 130,.0 7.4 5.65 20.40 1.*04 0.100 1.108 7.75 3*675 Cal ppm Mg ppm Na ppm K ppm Sr ppm Zn ppm Mn ppm Fe ppm Cu ppm. N % P ppm Om% ()ool Nos. 13, 25, 27, 28, 930,33, 37, 38 (2) Pool Nos. C-8, C-10, E-4,'E-ll,,F-l0, F-1ll, G-120 143 Chemical Composition of Aquatic Plants The public demand for clean waters must take into account the fact that surface water areas are like land areas in that some type of vegetation is going to occupy any suitable habitat. Thus, the more abundant the nutrient supply the more dense the vegetation, In an aquatic habitat this vegetation may take the form of bacteria, phytoplankton, filamentous algae, submersed weeds, emersed weeds, floating weeds, and marginal weeds. To understand the chemical complexities of the aquatic habitat of Lake Eufaula requires a knowledge of the chemical composition of the aquatic plants that occur within this environment. To more adequately understand the water, soil, aquatic plant relation- ship, data on chemical composition of plants from other aquatic environments are included for a comparative purpose. At this time it should be pointed out that aquatic weed in- festations in Lake Eufaula have been limited. The cause of this lack of rooted plant growth is unknown, but could possibly have been influenced by the yearly winter drawt-down period exposing most of suitable habitat to several weeks of freezing weather. Thus, sampling of plant species from similar environments was resorted to in an effort to more fully understand what was occurring in the shallow edge of Lake Eufaula. The diversity of chemical composition of two troublesome aquatic plant species, water hyacinth (Eichhornia crassipes) and alligatorweed (Alternanthera philoxeroides) from different environ- ments are illustrated in Figures 18 and 19. Collection Chemical composition as percent fdywih Site'C Ash Ca Mg Fe Mn P-N 0-0-0 ponds 0-8-0 ponds 8-8-0 ponds P. Pools Lake Seminole '65 Lake Seminole '67, 30.8 33.4 37.1 16.7 35.3. 15.2 0 .44 0 .515 0 41.5 15.3 1.60 39.8 17.9 1.74 34.8 16.5 1.04 Figure 18. Comparative chemical composition of entire water hyacinth plants fromsera hbit. Na 0- o80 0 1.03 1.43 0 .43 0 .301.14 0 .97 0 .49 0 .42 0 .20 0 .069 0 *061 0 .073 .195 0 .145 0 .161 0 .23 0 .23 .29 0 .936 0 *771 0 .861 0 1.115 0 .14 0 .27 0 .068.- 1.23 1.60 1.71 2.147 3.562 2,480 0 .08 0. .621 709 0 *632 0 *223 .0 ,270 0 .162 2.239 0 .205 1-*491. Collection Chemical comoiin spret oC r wih Site C Ash: Ca Mg Fe Mn p P. pools .'65 P. pools '66 P . pools '67 Lake Seminole '65 Lake Seminole Lake Eufaula '67 42.9 40.5 39.5 35.3 36.3 6.1 8.0 5.3 18.4 13.9 21.0 0 1.18 0 1.04 .30, 1.43 0- 1.35 0 .716 0 .336 0 ,471 0 .505 0 .307 0 .328 0 .98 0 .25 .164. .061 0 .072 0 .120 .157 0 .03 2 0 .072 O . 03 3 0 044 0 .022 0 053 0 *106 0 *049 0 090 0 o.170 *,107 0 .848 0 1.08 0- ,779 3.04 2.26 0 .185 3.00 ' Figue 1. Copartiv cheica comosiionof entire alligatorweed plants from several habitats. Na 0 508 .561 0 .091 0 .37 0 .35 0 .52 1.39 1.21 0 .36 4.56 2. 0 3.98 I LL ~ -~I~L~L Figure 19 Comparative chemical 'composition 146 Samples of water hyacinths were collected from Auburn University experimental ponds where no inorganic fertilization was practiced; where 80 lb. p205 was added per acre during summer months; and where 80 lb. P205 plus 80 lb* N was added per acre during summer months. Another set of water hyacinth samples was collected from Auburn University plastic pool series where only CaCO 3 Was added to precipitate suspended clay colloids in water. The final illustrated samples of hyacinths were collected from the Faceville landing area on the Flint river arm of Lake Seminole in 1965 and 1967. No sample of this plant from Lake Eufaula was included in this illustration because this species has never invaded this reservoir. Samples of alligatorweeds were collected from some Auburn University plastic pool series in 1965, in 1966, and in 1967. When this series was established in early 1965, each pool received the same amount of homogenous field soil and equal amounts of CaCO 3 to precipitate suspended clay colloids. Other samples were collected from Faceville area on Flint river arm of Lake Seminole in 1965 and in 1967. The final illustrated samples of alligatorweed were collected from upper portion of Lake Eufaula in 1967. An examination of these two illustrations shows the great diversity of chemical composition which can occur within a plant species grown under different environmental conditions. Apparently these two species are able to partially substitute one element, such as Mg, for another element, such as Ca. It is also apparent that alligatorweed was able to accumulate 147 an apparent luxury supply of K and possibly N in proportion to that quantity made available to the plant by the water and soil of its habitat. This last factor of nutrient consumption in re- lation to its availability in the environment is shown by alligator- weed composition from same series of plastic pools over a 3-year period (Table 34). These pools had no replinishment of nutrient supply other than from rain water, and their water overflow loss was approximately 50% each year. Comparisons of chemical composition of these two plants species in Lakes Eufaula and Seminole with experimental ponds and pools illustrates that these plants were able to accumulate vast quantities of elements from the continuously replinished supply available in river waters. Data on the averaged chemical element composition of the following plant species from several localities are given in indicated tables. Alligatorweed - Alternanthera philoxeroides Table 34 Water hyacinth - Eichhornia crossipes Table 35, 36 Waterwillow - Justicia americana Table 37 Smartweeds - Polygonum spp. Table 38 Parrotfeather - Myriophyllum brasiliense Table 39 Eurosion milfoil - Myriophyllum spicatum Table 40 Gross - Paspolum fluitans Table 41 Buttonbush - Cephalanthus occidentalis Table 42 Giant cutgrass - Zizoniopsis miliaceae Toble 43 148 Needlerush - Eleocharis acicularis Table 44 Eelgrass - Vallisnera americana Table 45 Curly leaf pondweed - Potamogeton crispus Table 46 - Bacopa sp. Table 47 White waterlily - Nymphaea tuberosa Table 49 Banana waterlily - Nymphaea mexicana Table 48 - Hydrocotyle sp. Table 47 Algae - Lyngbya sp. Table 49 Chara sp. Table 50 Nitella sp. Table 50 Included in the above listing of plants are certain species that have previously been reported in the thesis of Jerry B. Den- ton. Certain data from this thesis have been incorporated into the various tables on plant composition. These data were useful in- dicators of changes in plant composition with time and with changes in sampling sites within the same general area of a given habitat. Also included in the tabular presentation are averaged com- positions of the following species of algae as presented in the dissertation of Claude E. Boyd (Table 51). Filamentous forms Planktonic forms Chara sp. Microcystis sp. Pithophora sp. Aphanizomenon sp. Clodophora sp. Anabaena sp. Spirogyra spp. Euglena sp. Giant Spirogyro sp Rhizoclonium sp. 149 Filamentous forms Hydrodictyon sp. 0edogonium sp. Mougeotia sp. Lyngby sp. Nitella sp. These data of Boyd's have been particularly useful in com- parative studies of differences in composition of algae samples obtained by separation with No. 25 bolting silk (Boyd) and separation by use of 8 . Millipore filter. This has emphasized that composition is varied within size groups of a species of alga and that other constituents besides the alga cells may have been retained by the Millipore filter. 150 Table 34 Averaged chemical element composition of alligatorweed collected from plastic pools and from Lakes Eufaula and Seminole during period 1965-1967 ,Plasti pool '65 6.108 Area Year Ash % Ca ppm Mg ppm Na ppm K ppm Sr PPM Zn ppm Mn ppm Fe ppm Cu ppm Pb PPM Cr ppm Ni ppm Mo ppm Co 0ppm Cd ppm c % P ppm pool 166 8.04 10450.0 4710.0 5610.0 1210000 90 88.5 720.0 16400 43.0 14.5 21.0 8.5 6.5 1.25 1.001 40.48 492.5 Lake '65 18.39 Seminole 166-167 13.90 ---~ ----_- ~Plastic pool 167 5.31 3000.0 5050.0 915. 0 3600.0 9.0 255.0 328.0 610*. 27.5 9.0 29.*0 10.0 1.5 .799 900.0 (1 ppm = .ig/g dry weight of plant. 11760.0 3360.0 5080.0 13900.0 160.0 320.0 25000 38.0 .848 42.*969. 1060o.0 . - ft 14300.0 3070.0 3700. 0 45600.0 90,6 0 440.0 720.0 15.0 3,045 39. 515 1700.00 13478.0 3282.0 3505.0 25006.0 4.98 90.57. 224.3 1196.0 112.4 8o78 24.08 7.86 7.95 6.09 3,88 2.260 35.34 1076,000 aLak Eufaula 166-67 20.97 7155.0 5979*.0 5200.0 39844.0 6.64 135.64 528.4' 1574.2 80.6 17.55 42.99 10.52 10.03 5.92 1.95 3.003 36.34 1852.00 151 Table 35 Averaged chemical element composition of water hyacinth collected from Auburn University experimental ponds in 1967. Area 0.1 acre earthen ponds Treatment 0-0-0 0-8-0 8-8-0 Collection Site Edge Center Edge Center Edge Center % Moist. 93.85 86.81 92.45 94.03 92.48 93.98 Ash % 37.04 33.06 17.63 15.89 17.19 13.25 Ca ppm 3750 5120 4850 4950 5617 5450 Mg ppm 8350 7700 11050 9600 10650 12200 Na ppm 783 817 5800 6633 5987 8200 K ppm 12467 12067 20333 11733 18933 15200 Sr ppm 4.3 3.0 6.0 5.7 5.7 9.3 Zn ppm 540.0 573.3 320.0 163.3 285.0 175.0 Mn ppm 2067 1933 797 580 683 543 Fe ppm 15250 13300 4600 4100 4380 1600 Cu ppm 177 157 177 217 167 170 Pb ppm 8.0 5.3 2.7 10.7 8.7 4.0 Cr ppm 167 176 82 71.3 86.7 78.0 Ni ppm 30.7 33.3 20 14 14.7 24.7 Co ppm 2.8 6.47 1.00 1.67 1.4 1.2 Cd ppm 1.07 1.13 .80 .67 .4 1.0 N % 1.092 .781 .663 .880 1.012 .710 C % 32.35 30.86 36.89 37.13 37.44 33.24 P ppm 767 695 2140 1773 1553 1350 (1) PPM = yg/g dry weight of plant. 152 Table 36 Averaged chemical element composition of water hyacinth collected from plastic pools in 1965 and from Lake Seminole during period 1966-67 Area Plastic Pools Lake Seminole Year '65 '65 '66-67 Plant Part Shoot Root Shoot Root Whole Ash % 14.557 16.113 15.930 20.00 16.48 Ca ppm 19480.0 12570.0 19910.0 14830.0 10400.0 Mg ppm 10020.0 9360.0 4000.0 5810.0 4200.0 Na ppm 5020.0 7630.0 1050.0 3410.0 2700.0 K ppm 20870.0 22070.0 41650.0 29600.0 24800.0 Zn ppm 140.0 450.0 50.0 160.0 155.0 Mn ppm 890.0 1810.0 3940.0 1590.0 680.0 Fe ppm 120.0 2280.0 250.0 2840.0 2900.0 Cu ppm 21.0 41.0 11.0 15.0 90.0 Pb ppm 16.0 Cr ppm 80.0 Ni ppm 12.0 Mo ppm 6.0 Co ppm .4 N % 1.371 .860 2. , 1.868 1.491 C % 41.23 41.936 40.721 38.960 34.81 P ppm 1920.0 1310.0 1770.0 1470.0 2050.0 (1) PPM = pg/g dry weight of plant. 153 Table 37 Averaged chemical element composition of waterwillow collected. from plastic pools,'from Bartlett's Ferry Reservoir and from Lake Seminole during period 1965-67 Area Year Ash% Ca ppm Mg ppm Na ppm K ppm Sr ppm Zn ppm Mn ppm Fe ppm Cu ppm Pb ppm Cr ppm Ni ppm Mo ppm Co ppm Cd ppm P ppm Plasti*c Pools '67 10.14 720000 1100000 800.0 11200.0 23.0 190.0 300.0 660.0 44.0 200 16.0 10.10 0.6 2.2 1. 41.71 2300.0 Bartlett 's Ferry '67 12.39 16920.0 8490.*0 1730.0 27067.0 12.0 254.0 780.0 820.0 564.0 6.4 35.6 8.4 13.6 10.4 2.782 42.65 2133.0 (1) PM =dry weight of plant.' Lake '65 17640o0 2990.0 159000 26520.0 20.0 830.0 1920.0 900 3.951 41.629 2410.0 Seminole '66-67 14.98 1356000 4691.0 2292.0 26460.00 6.2 108.4 733.6 2536.*0 142.0 8.0 18.8 12.0 5.12 2.553 38.39 1767.0 r r. rr".rr r - - it (1 PM p/ 154 Table 38 Averaged chemical element composition of smartweeds collected from Lake Eufaula during 1966-67 Area Lake Eufaula Year '66-67 Ash % 15.24 Ca ppm 8150.0 Mg ppm 4550.0 Na ppm 1352.0 K ppm 19163.0 Sr ppm 20.2 Zn ppm 142.2 Mn ppm 599.4 Fe ppm 2074.0 Cu ppm 64.9 Pb ppm 12.0 Cr ppm 64.9 Ni ppm 18.9 Mo ppm 10.14 Co ppm 7.66 Cd ppm 4.28 N % 1.529 C % 29.57 P ppm 1488.0 (1) PPM = pg/g dry weight of plant. 155 Table 39 Averaged chemical element composition pf parrotfeather collected from plastic pools and from Lake Seminole during 1966-67. Area Year Ash % Ca ppm Mg ppm Na ppm K ppm Sr ppm Zn ppm Mn ppm Fe ppm Cu ppm Pb PPM Cr ppm Ni ppm Mo ppm Co ppm Cd ppm Pppm Plastic Pool '65 9.47 21490.0 7780.0 5270.0 15370.0 170.0 700.*0 360.0 22.0 1.e347 43.253 1730.0 (1) PPM.= pg/g dry weight of plant. Lake Seminole 165 10.82 22600.0 1850.0 2660.0 16800.0 40.0 1320.0 690.0 7.0 1.580 42.798 960.0 '66-67 27.62 34.100.0 731 0 2640.0 313500 7.5 32. 0 965.0 20,2.5 12.o5 9.5 4..5 40 1 91.00 19.0 2.7 1.145 44.a96 789000 at, ,;,, 156 Table 40 Averaged chemical'.element composition of Eurasian milfoil1 collected. from plastic pools and from Lake Seminole during period 1965-67 Area Ye ar Ash % Ca ppm mg ppmn Nia PPM K ppm Sr ppm Zn ppm Mn ppm Fe ppm Cu ppm Pb ppm Cr ppm Ni ppm Mo ppm Co ppm Cd ppm C % .P ppm Plastic Pools '65 13.88, 19030.0 349000 12800.0 18000.*0 280.0 173000 2120.0 25.90 2.490 42.93 2930.0 Plastic Pools '66 6e68 6105.0 3723.0 4207.0 77000 7.5 186.5 .9500 4100.0 78.5 49*5 90.0 16.0 9.0 6.5 1,917 27.82 600.0 Lake Seminole '66-67 24.*97 25960.0 1503 .0 3719.0 8671.0 5.59 120.4 1185.0 2991.0 107.5 13.*45 163.5 26.*61 12.25 9.33 2.61 2.280 34.02 1365.00 ( PPM g/g dry weight of plant. 157 Table 41 Averaged chemical element composition of Paspalum fluitans collected from Lake Eufaula during period 1965-67 Area Lake Eufaula Year '65 '66-67 Ash % 12.71 18.91 Ca ppm 2600.0 1500.0 Mg ppm 2170.0 3133.0 Na ppm 2200.0 1740.0 K ppm 25400.0 22453.0 Sr ppm - 1.33 Zn ppm 40.0 198.7 Mn ppm 240.0 1076.0 Fe ppm 980.0 896.7 Cu ppm 20.0 32.7 Pb ppm 4.53 Cr ppm 107.3 Ni ppm 20.0 Co ppm 5.67 Cd ppm 2.60 N % 1.907 2.122 C % 48.84 34.95 P ppm 2020 0 870.0 (1) PPM = pg/g dry weight of plant. 158 Table 42 Averaged chemical element composition of buttonbush collected from Lake. Eufaula Area Lake Eufaula Year '66 Ash % 8.02 Ca ppm 1100.0 Mg ppm 2035.0 K ppm 12320.0 Sr ppm 2,0 Zn ppm 60.0 Mn ppm 140.0 Fe ppm 160.0 Cu ppm 105.0 Pb ppm 32.0 Cr ppm 1.0 Ni ppm 3.0 Mo ppm 5.0 Co ppm 8.0 Cd ppm 2.0 N % 1.970 C % 10.6 P ppm 2365.0 (1) PPM = pg/g dry weight of plant. 159 Table 43 Averaged chemical element. composition of giant cutgrcss. collected from Lakes Eufaula and Seminole during 1966-67 Area Year Ash % Ca ppm Mg ppm Na ppm K ppm Sr ppm Zn ppm Mn ppm Fe ppm Cu ppm Pb ppm Cr ppm Ni ppm Mo ppm Co ppm Cd ppm N% c % p ppm Lake Eufaula 166-67 14.03 1483.0 1662.0 1800.0 3090000 1.3- 176.7 361.3 1993.0 38.3 7.3 90.7 90 3.3, 1.5 1*789 41.59 1957.0 (1)PPM g/g dry weight of-plant. Lake Seminole 166-67 104.20 4217.0 972.0 1512.0 19332.0 1.5 134.2 495.5 2022.0 105.0 10.25 67.0 17.0 10.0 .*93 1.527 43.87 1020.0 160 Table 44 Averaged chemical element composition of needlerush collected from plastic poois during period 1965-1967 Area Year Ash% Ca ppm Mg ppm Na ppm K ppm Sr ppm Zn ppm Mn ppm Fe ppm Cu ppm Pb ppm Cr ppm Mo ppm Co ppm Cd ppm P ppm Plastic Pools 165 8.423, 5170*. 2640.0 5420.0 37950.0 400.0 1170.0 1880. 22*.0 1.496 44.*09 1850.0 1)PPM )g/g dry weightof plant, Plastic Pools 66-67 5.44 1430.0 682.0 2750.0 8745,0 4.75 120.0 190.0 1900 13.5 17.0 14.0 9.0' 0 10.0 085 44o84 1162.0O 161 Table 45 Averaged chemical element composition of eelgrass collected from plastic pools during period 1965-1967 Area Plastic Pools Plastic Pools Year ' 65 '66-67 Plant part Shoot Root Whole Ash % 20.62 21.91 25.80 Ca ppm 7870.0 6440.0 4212.0 Mg ppm 8730.0 1980.0 6395.0 Na ppm 10670.0 7680.0 7566.0 K ppm 42400.0 14700.0 15772.0 Srppm - 4.5 Zn ppm 80.0 180.0 233.0 Mn ppm 2920.0 1890.0 1615.0 Fe ppm 490.0 5770.0 6400.0 Cu ppm 16.0 61.0 85.0 Pb ppm - 12.7 Cr ppm - 237.7 Ni ppm - 45.7 Mo ppm - Co ppm - 10.0 Cd ppm - 7.25 N % 1.887 1.413 1.555 C % 39.77 36.56 P ppm 2120.0 1760.0 1001.0 (1) PPM = pg/g dry weight of plant. 162 Table 46 Averaged chemical element composition of Potamogeton crispus collected from Lake Seminole during 1965-67 Area Lake Seminole Year ' 65 '66-67 Ash % 26.49 20.27 Ca ppm 27600.0 28579.0 Mg ppm 840.0 770.0 Na ppm 1860.0 3302.0 K ppm 26600.0 15899.0 Sr ppm 7.25 Zn ppm 60.0 153.4 Mn ppm 1170.0 1762.0 Fe ppm 3790.0 1711.0 Cu ppm 1.0 109.1 Pb ppm 7.0 Cr ppm - 74.1 Ni ppm - 22.37 Mo ppm - 10.3 Co ppm. 8.73 Cd ppm - 4.45 N Y 3.433 1.999 C % 42.63 36.81 P ppm 1240.0 1649.0 (1) PPM = pg/g dry weight of plant. 163 Table 47 Averaged 'Chemical element composition of Bacop sp. and Hyrootyl sp. collected from Lake Seminole in 1967 Lake Seminole .167 Area Year Species Ash % Ca ppm Mg ppm Na ppm K ppm Sr ppm Zn ppm Mn ppm Fe ppm Cu ppm Pb ppm Cr ppm Ni ppm Co PPM Cd ppm C % P ppm Bacop.asp. 21.53 4460000 800.0 15000.0 8400.0 5.0 150.0 10700.0 4300.0 370.0 2.0 84.0 20.0 14.0 10.0 2.155. 34,75 1450.0' ()PPM = g/g dry weight of plant.' Hydrocotyl sp 20.78 9000 3300 2700 31600 4.0 200 80 4360 100 20 90 22 2.0 0.4 3,148 3 5.94 1900 164 Table 48 Averaged chemical element composition of white waterlily and banana waterlily from Lake Seminole in 1967 Lake Seminole '67 Are a Year Species Ash %o Ca ppm Mg ppm No ppm K ppm Sr ppm Zn ppm Mn ppm Fe ppm Cu ppm Pb ppm Cr ppm Ni ppm Co ppm Cd ppm N % C% P ppm White waterlily 7.01 8500.0 12400.0 12400.0 8000.0 1.0 130.0 80.0O 200.0 430.0 2.0 6.0 6.0 10.0 10.0 3.650 42.22 1630.0. (1) PPM = jg/g dry weight of plant. Banana waterlily 6.66 5200 1160 7700 1400 2.4 100 980 700 122 2.0 52 8.0 0.4 0.2 1.070 41.34 860.0 165 Toble 49 Averaged chemical element composition of Lyngba spp. collected from Auburn University experimental ponds in 1965 and from Lake Eufoula in 1967 Area Year Ash % Ca ppm Mg ppm No ppm K ppm Sr ppm Zn ppm Mn ppm Fe ppm Cu ppm Pb ppt Cr ppm Ni ppm Co ppm Cd ppm N % C % P ppm Exp. ponds '65 72,11 1900 2000 700 15000 0.4 430 1180 16400 400 70 700 40 18 24 .886 11.36 1800 (1) PPM = pg/g dry weight of plant. Lake Eufaula '67 17.20 4500.0 1400.0 600.0 4200.0 5.01 40.23 310.0 166 Table 50 Averaged .chemical element composition of Chara spp. and Nitella spp. collected :from Auburn University experimental Ponds -in 1965 and! from Lake Seminole in 1967 Exp. Ponds 165 Lake Seminole 067 Chara 43.41 58.09 80300.0 5830.0 9200.0 1930.0 1300.0 3075.0 23500.0 21000 395 89.0 395.0 2926.0 2360.0 2520o0 910000 19.0 650.0 28.0 395.0 41.0 Ash % Ca PPM Mg ppm Na PPM K ppm Sr ppm Zn ppm Mn ppm Fe ppm. Cu ppm Pb ppm Cr ppm Ni ppm Mo. ppm Co.: ppm Cd ppm c % P ppm 16.0 11.0 1.765. 15.20 1900 .0 Area Year (1) PPM = pg/g dry weight of plant. Exp. Ponds Lake Seminole '65 '67 Nitelha 19.11 22.27 18,900 19,508.0, 9500.0 29. 2800.0 4858. 37,300.0,,4179.0 5.42 33.99 560.3 4396.0 30.74 12*. 28.6 6.21 4.29 4.03 1.51 2.70 2*337 38.-43 3.4.84 2300.0 954.0 2d46 29.28 2500.0 ~u r~~E~m IrU n311,11 167 Table 51 Chemical composition of some algae from ponds and lakes in Southeastern United States Averaged composition as percent dry weight for given species. Analysis Chara Ash 43.4 C. 29.3 N 2.46 F.25 S.55 Ca. 8.03 Mg .9? K 2.35 Na .13 27.77 35.38 2.57 .30 1.42 3.82 .20 3.06 .07 23.38 35.27 2.30 .56 1.58 1.69 .23 6.08 .18 13.06 42.40 .20 .27 .57 .45 .92 1.42 Giant 13.86 41.16 2.35 .23 .24 .84 .30 .99 1.43 17.36 39.10 3.46 .43 .27 .52 .21 1.90 .09 17.94 39.96 3.87 .24 1.41 .69 .17 4.21 .38 12.69 40.84 2.64 .08 .15 .44 .16 3.03 .06 Averaged composition as ppm dry weight for given species Fe 25?0 2836 1040 1368 1793 1820 1373 1645 Mn 2926 829 2300 1641 1658 1687 1963 1729 Zn 89 29 10 72 46 89 129 119 Cu 19 23 190 47 34 75 114 75 B 6.7 65 84.6 4.2 4.3 1.8 8.1 Averaged composition as percent dry weight for given species Analysis Mou-ieotia Lyngbya Nitella Microcystis Aphanizomenon Anaboena Euglena Ash 14.54 17.20 19.11 6.2 7.21 5.19 4.12 C 40.74. 40.23 38.43 46.46 47.65 49.70 48.14 N 1.77 5.01 2.70 8.08 8.57 9.43 5.14 .25 .31 .23 .68 1.17 .77 .67 S .36 .28 ..34 .27 1.18 .53 .19 Ca 1.68 .45. 1.89 .53 .73 .36 .05 Mg .57 .14 .95 .17 .21 42 .07 K 1.20 .42 3.73 .79 .68 1.20 .34 Na .49 .04 .28 .04 .19 .18 .02 Averaged composition as ppm dry weight for given species Fe 60 5230 2388 2751 167 80 240 Mn 1080 3866 2180 322 .833 800 1545 Zn 52- 171 240 48 120 0 73 Cu, 143 101 39 37 187 70 290 B 8 112 9.8 3.6- 0 3.8 ri-unopnora apirogyra . anizocionium nyaroamc-cyon veuogonium Fithmnhnrn Clndnnhrn R h i tr me- I mn i i i7d 14%YA-re-,A4 e-+unri I MaeInnnn 4 1 tyn 168 Chemical Composition of Freshwater Fish Fishing success in Lake Eufaula has been phenomonal for years 1964, 1965, 1966, and 1967. The major catches have been largemouth bass (Micropterus salmoides), black crappie (Pomoxis nigro-maculatus) and white crappie (Pomoxis annularis). While the fishermen have concentrated their efforts on the 3 species listed above, other edible species are abundant in the reservoir as shown in Table 52 furnished by Fisheries Division, Alabama Department of Conservation. However, in accounting for the chemical composition of the aquatic environment within Lake Eufaula, it is necessary that the composition of as many of these species as possible be determined. A limited amount of comparative chemical composition data on freshwater fishes from Lake Eufaula, Lake Seminole and Auburn Univer- sity experimental ponds will be presented in this report. More de- tailed and complete analyses of the entire body of several species of fish will be presented in theses now in preparation by Beverly Clement and by Roland Reagan. It was imperative in developing these analytical techniques to sample fish from different types of habitats, and it was equally im- portant that each analysis be representative of the content of the entire fish. The importance of these two requirements can be illus- trated by data on chemical composition of channel catfish (Ictalurus punctatus) from ponds receiving no fertilization, from ponds receiving P only fertilization (Table 53), and on the chemical composition of head portion, middle portion, and tail portion as shown in Table 54. 169 Table 52 FISH POPULATION SAMPLE SUMMARY LAKE EUFAULA AUGUST 11-12, 1966 Two acre, block-net shoreline sample, east bank, 1 mile below Hatchechubee Creek Landing. Number Weight Species Collected (Pounds) I. Largemouth Bass 315 21.09 2. Spotted Bass 1 .16 3. Coosa Bass 1 .20 4. White Bass 37 .53 5. Chain Pickerel 4 3.92 6. Channel Catfish 163 9.26 7. White Catfish 192 3.50 8. Brown Bullhead 21 5.96 9. Snail Catfish 11 1.56 10. Flat Bullhead 13 .54 11. Bluegill 1,395 25.68 12. Redear 75 7.51 13. Redbreast 75 5.40 14. Longear 14 .55 15. Green Sunfish 29 .62 16. Warmouth 118 2.43 17. Black Crappie 255 6.40 18. White Crappie 11 1.29 19. Yellow Perch 2 .04 20. Gizzard Shad 19,505 240.30 21. Threadfin Shad 5,351 29.41 22. Carp 38 17.69 23. Golden Shiner 66 3.65 24. Blacktail Shiner 3 .07 25. Taillight Shiner 322 .58 26. Brook Silversides 12 .03 27. Gambusia 1 T 28. Pugnose Minnow 7 T 29. Tadpole Madtom 19 .05 Totals 28,056 388.42 170 Table 53 Averaged chemical element composition of channel catfish randomly selected at draining time from Auburn University experimental ponds, 1966 Treatment 8-8-0 0-0-0 8-8-2 % Ash 26.10 22.71 19.15 Ca ppm (1) 42716 34349 37080 Mg ppm 2163.7 2132.3 2148 Na ppm 5419.7 5448.3 5915.3 K ppm 6037.7 6382.3 6616 Sr ppm 5.0 4.0 4.67 Zn ppm 148.3 93.7 155.7 Mn ppm 37.0 35.7 47.0 Fe ppm 271.0 168.0 149.3 Cu ppm 42.0 58.3 31.7 Pb ppm 18.0 16.0 15.33 Cr ppm 12.0 18.0 8.33 Ni ppm 5.27 7.67 7.0 Mo ppm 8.27 5.67 7.33 Co ppm 4.27 2.80 2.67 Cd ppm 2.80 2.47 2.67 N % 10.415 11.778 11.331 P ppm 46427 38124 40830 (1) ppm = pg/g dry weight of fish. 171 Table 54 Averaged -chemical element composition(1 of he ad, middle, and tail portions of channel catfish collected at draining time from Aublurn University experimental ponds, 1966 Whole f ish 37381 2116 5521 6220 4.5 131 39.3 191.6 42.55 16.1 12.66 6.55 7.00 3.15 2.60 11,.174 41119 Head- 503 73 2534 6942 4779 6.9 140 54.3 181 19 17 17.6 7 9.'6 4.3 2o66 8.283 62746 Body portions Middle 34153 2023 5323 6756 4.0 90 32 223.3 66 16.6 10.6 5.6 6.0 2.66 12.179 34494 ( p pg/g dry weight of fish Ca ppm Mg ppm Na p'pm K ppm Sr ppm Zn ppm Mn ppm Fe ppm Cu ppm Pb ppm Cr PPM Ni ppm Mo ppm. Co ppm Cd ppm P ppm Tail 29284 1887 4517 7501 3.17 167.7 33.3 184.0 46.0 15.7 1000 7.27 3.33 2.60 13.060 28140 1 "1 ppm 172 Data on channel catfish collected from Lakes Eufaula and Seminole are summarized in Table 5?. Other species of freshwater fish for which chemical composition data will be presented include the following: Largemouth bass (Micropterus salmoides) Table 56 Bluegill bream (Lepomis macrochirus) Table 57 Green sunfish (Lepomis cyanellus) Table 58 Redbreast sunfish (Lepomis auritias) Table 58 Redear sunfish (Lepomi s microlophus) Table 58 Black crappie (Pomoxis nigro-maculatus) Table 59 White crappie (Pomoxis annularis) Table 59 Warmouth (Chaenobryttus coronarius) Table 60 Yellow bullhead catfish (Ameiurus natalis) Table 61 Gizzard shad (Dorosoma cepedianum) Table 62 Golden shiner (Notemigonus crysoleucas) Table 62 Fathead (Pimephole s promelas) Table 63 It will be noted that composition data on these species are reported by inch-group of total length of the fish. The sizes of largemouth bass reported in Table56 indicate that certain !elements, such as Ca, show slight increases in content with length, whereas other elements such as Zn, Cu, and Fe show some decrease in content with total length. Bluegill datm. indicate a marked increase in Co and Mg content through 6 inch groups and then a decrease in inch groups 7 and 8 (Figure 20). Other elements in the bluegill analyses show similar trends. U Ik 0) *r a) a a U' 4JI 0) 4-1 ) U a;) .5 .4 .3 .2 .1 In. Gp.2 6 5 4 3 1i In. Gp2 Figure 20. 4 3 4 5 6 7 8 4 6 7 173 Ave-rages and rangesof calcium and magnesium concentrations in-various inch groups of bluegills collected from ponds and reservoirs in Alabama .and Georcria. I II II III 174 These two species were chosen to illustrate tottl length- chemical composition trends because more different lengths have been analyzed. However, the numbers of individuals included in each inch- group were too small to firmly establish any definite pattern. Available data on other species are too meager to make any such com- parisons at present. These and other unusual features of chemical composition trends in several species of freshwater fish will be ex- plored in the two theses now in preparation. As pointed out earlier in this Section, the data given in the tables are averaged analyses of fish collected from various environments. Of particular interest are those data on metallic element composition which appear to be high values for animals. Comparative metallic element composition data of four species collected from experimental ponds are given below. pg/g dry weight Element Fathead C. Catfish Largemouth bass Bluegill Zn 173 131 107 85 Cu 52 42 15 45 Pb 12 16 5 2 Cr 11 12 8 18 Ni 5 6 4 6 Cd 2 2 1 1 175 Table 55 (1) Averaged chemical element composition of channel catfish randomly collected by rotenone and electricity from Lakes Eufaula and Seminole in 1966-67 % Moist 81.78 % Ash 21.14 Ca ppm 37360 Mg 1883.3 Na 4016.3 K 7067 Sr 4.5 Zn 87.3 Mn 76.0 Fe 449.3 Cu 35.0 Pb 14.67 Cr 46.7 Ni 9.33 Mo 4.0 Co 2.17 Cd 1.53 N % 10.751 C % 36.82 P ppm 32366 (1) 1 ppm = 1 Vg/g dry weight of fish 176 Table 56 (1) Averaged chemical element composition of various inch-groups of large- mouth bass randomly collected by rotenone, dynamite, and electricity from Lakes Eufaula and Seminole during 1966 and 1967 In. gp. 3 4 7 8 9 10 % Moist. 75.88 77.82 74.96 74.88 % Ash. 18.42 15.85 19.68 18.77 20.14 19.21 Ca ppm 33390 24895 36239 20540 41750 44750 Mg ppm 1906.7 1768 2101 1872 2050 1825 Na ppm 2855 1598 3736 1390 4450 4200 K ppm 13920 14300 6378 11700 12700 11800 Sr ppm 20.13 6.85 2.5 4.0 25.0 32.5 Zn ppm 188.0 82.5 77.0 108.0 12.5 7.5 Mn ppm 35.33 14.0 6.0 22.0 4.5 4.0 Fe ppm 185.2 77.5 63.0 23.0 125.0 80.0 Cu ppm 292.2 15.0 20.0 24.0 177.5 220.0 Pb ppm 5.17 2.5 22.0 12.0 5.5 6.5 Cr ppm 20.33 12.5 1.0 35.0 16.0 13.5 Ni ppm 49.7 3.25 8.0 4.5 12.5 10.0 Mo ppm 3.0 Co ppm 10.5 7.5 1.5 20.0 6.5 7.5 Cd ppm .9 .75 2.3 1.0 .5 .55 N % 10.62 11.53 9.90 10.18 9.40 10.33 C % 41.15 44.55 43.92 42.70 35.05 41.02 P ppm 30626 29835 37827 40400 38500 (1) 1 ppm = 1 pg/g dry weight of fish 177 Table 57 Averaged chemical element composition ( 1 ) of different inch-groups of bluegills randomly collected by rotenone, dynamite, and electricity from Lakes Eufaula and Seminole during 1966 ond 1967 Inch Gp. 2 3 4 5 6 7 8 % Moist. 76.83 76.33 75.75 72.91 74.55 68.17 79.63 % Ash 14.96 18.90 20.76 22.99 22.58 18.25 15.13 Ca ppm 19557 35772 43820 28600 49000 26400 20605 Mg ppm 1499 1624 1824 1872 2140 1461 1209 Na ppm 1665 2035 2700 1807 4175 2398 1520 K ppm 12057 11360 12200 9270 12500 7532 7433 Sr ppm 7.5 16.25 30.0 6.5 25.0 7.88 5.5 Zn ppm 113.0 227.0 458.0 125.5 40.0 88.3 73.3 Mn ppm 71.0 76.5 55.6 107.5 52.5 54.1 39.7 Fe ppm 188.1 219.5 1084.0 43.5 345.4 111.4 147.2 Cu ppm 153.5 38.25 208.4 29.5 142.5 75.8 14.67 Pb ppm 3.43 3.80 5.20 9.0 3.5 6.79 3.0 Cr ppm 20.9 20.5 29.0 22.5 25.0 13.57 12.17 Ni ppm 10.57 88.25 136.6 7.0 54.0 7.64 3.17 Mo ppm 4.0 Co ppm 11.0 12.75 6.4 24.0 6.5 13.77 11.5 Cd ppm .84 .85 .20 1.0 .60 1.56 .68 N % 10.42 9.25 9.70 8.65 9.98 8.87 8.29 C % 44.35 43.57 40.86 42.65 38.08 45.27 47.54 P ppm 24846 28420 33800 31850 40400 29283 24960 pg/g dry weight of fish (1)1pm= 178 Table 58 (1) Averaged chemical element composition of various species of sunfish family collected by rotenone, dynamite, and electricity from Lakes Eufaula and Seminole' in 1965 and 1966, Species In...Gp. % Moist. %Ash Ca ppm Mg ppm Na ppm K ppm Sr ppm Zn ppm Mn ppm Fe ppm Cu ppm Pb ppm Cr ppm Ni ppm MO ppm Co ppm Cd ppm C % P ppm Green Sunfish 4 81.08 22.67 39415 2475 4110 5884 4.0 132.0 42.0 130,.0 44.0 15.0 4.0 10.0 3*.0 1.5 2.2 9 *240 34.30 46700 (1) 1 ppm = 1 pg/g dry weight of fish Redbreast .5- 79,77 29.80 49502 2569 4670 5744 4.5 99.0 .36.0 .80 .0 1400 25.0 5 '.0 9.0 4.0 11.0 3*3 10.285 33.69 53238 Re dear 5 79.58 22.25 42015 1955 3758 9372 10.0 58.5 41.0 225.0 53.0 13.5 9.*5 36.0 2.0 4.5 2.25 9.35 41.16 31733 179 Table 59, Averaged chemical element composition of two species of crappie collected by rotenone, dynamite, and electricity from Lakes Eufaula and Seminole in 1965 and,1966 Species In. Gp. % moist. % Ash Ca ppm Mg ppm Na ppm K ppm Sr ppm Zn ppm Mn ppm Fe ppm Cu PPM Pb PPM Cr ppm Ni ppm Co ppm Cd ppm NY C % P ppm White crappie 8 89.27 19.26 35492 1821 2802 5477 62.0 17.0 113.0 7,0 400 1. 2 300 9,480 40,47 9. 77.65 24.5 9 38500 2035 1.0 195.0 30.0 260.0 30.0 14,0 18.0 120 3.0 11.0220 38.26 475,20 (1) 1 ppm 1 pg/g dry weight of fish Black crappie 7 81.24 27.97 50436 2382 4577 6071 6.0 61 21 70 23 20 8 7 2 1.5 2."0 10,927 36.63 51837 180 Table 60 Averaged chemical element composition ( l ) of warmouth collected by rotenone, dynamite, and electricity in Lakes Eufaula and Seminole in 1966 and 1967 In. Gp. 4 5 % Moist. 75.93 74.82 % Ash 19.78 26.93 Ca ppm 41500 43618 Mg ppm 1770 2270 Na ppm 4200 4016 K ppm 11400 5511 Sr ppm 50.0 Zn ppm 100.0 87.0 Mn ppm 55.0 55.0 Fe ppm 320.0 210.0 Cu ppm 100,0 55.0 Pb ppm 8.0 20.0 Cr ppm 13.0 14.0 Ni ppm 55.0 9.0 Mo ppm 6.0 Co ppm 10.0 1.5 Cd ppm 1.1 2.0 N % 10.57 10.765 C % 41.57 40.58 P ppm 39600 40629 (1) 1 ppm= pg/g dry weight of fish 181 Table 61 Averaged chemical element composition of various inch groups of yellow bullhead catfish collected by rotenone,,dynamite and electricity from Lakes Eufaula and Seminole in 1966 and 1967 Location In. Gp. %Moist0. % Ash Ca ppm Mg ppm Na ppm K ppm Sr ppm Zn ppm Mn ppm Fe ppm Cu ppm Pb ppm C r ppm N i ppm Mo -PPM Co ppm Cd ppm N % C% P ppm Lake Eufaula 6' 81.20 16.72 36500 1750 3300 15600 2500 50.0 56.0 480,.0 4.0 35.0 96.0 3.0 1*8 12.14 41.34 27400 L.Seminole 6 80.06 22.48 40162 1821 4390 6725 50.0 65.0 650.0 40.0 15.0 8.0 ).9.0 6.0 1.5 i,*0 ~~3 .0 9.*448 43.76- 39228 L.Seminole 7 78.32 24,637 39508 1961 5137 5791 63. 115 .0 700,.0 46.0 17.0 11.0, 6.0 6.0o 2.0 1.8 10. 750 39.87. 31523 (1) 1 ppm = 1 pg/g dry weight of fish wr - 182 Table 62 Averaged chemical element composition of gizzard shad and golden shiners collected by rotenone from Lake Eufaula in 1965 and 1966 Species % Moist. %o Ash C a ppm M g ppm Na ppm K ppm Sr ppm. Zn ppm Mn ppm Fe ppm Cu ppm Pb ppm Cr ppm Ni ppm Mo ppm Co ppm Cd ppm c % P ppm Gizzard shad 79.41 20.43 39229 1723 3893 9560 12.33 101.75 64.75 876.25 92.75 8.25 23.5 67.5 7.0. 4.37 2.35 10.41 39.76 (1) 1 ppm = pg/g dry weight of fish shiners 80.76 20.41 45750 202.5 3223 9590 35.0 56.6 38.0 360.0 115.6 9.0 14.33 57.3 9.0 1.4 9.92 40.49 30443 183 Table 63 Averaged chemical element composition of fathead minnow collected by rotenone from Auburn University experimental ponds in 1966 In. Gp. 2 3 4 Ca ppm 37360 30754 34052 Mg ppm 2615 1417 2016 Na ppm 5136 1650 3742 K ppm 5800 10660 7744 Sr ppm 4.85 5.0 4.92 Zn ppm 195.0 140.0 173.0 Mn ppm 140.3 62.0 109.0 Fe ppm 1293.3 287.5 790.0 Cu ppm 37.7 74.0 52.2 Pb ppm 17.3 3.75 11.9 Cr ppm 9.66 14.0 11.4 Ni ppm 6.33 4.0 5.4 Mo ppm 5.33 Co ppm 2.83 6.25 4.2 Cd ppm 2.93 1.20 2.24 N % 6.873 9.56 7.96 C % 39.196 47.2 42.40 P ppm 34324 24830 30526 1 ppm = 1 pg/g dry weight of fish 184 SUMMARY The determination of chemical and physical characteristics in water, bottom muds, and aquatic life within Lake Eufaula and its Chattahoochee river headwaters and tailwaters started in May, 1965 and continued through November, 1967. Lake Eufaula, which is the 10th downstream impoundment on Chattahoochee river, is a multipurpose, run-of-river, reservoir, with surface area of 45,000 acres, an average depth of 20 feet, and a drainage area of 7,460 square miles. The averaged rate-of-flow since its impoundment in 1963 has been 10,800 cfs. During 1930's this river was known as the "muddy Chattahoochee" and often had a silt load in excess of 400 ppm. The turbidity during the course of this study has ranged from 3 to 68 ppm indicating the influence of upstream impoundments as sediment basins, but more importantly it domonstrates the change from row crop farming to pasture lands and wood lots. Early emphasis in this study was on water chemistry and was concerned with temperature, dissolved oxygen, and stratification relationships. During summers of 1965 and 1966 surface water tempera- tures often approached and occasionally exceeded 300C, while bottom waters at depths of 75+ feet were 60 to 80 cooler. Dissolved oxygen concentrations in surface waters often approached, but rarely ex- ceeded saturation. During hot, dry periods dissolved oxygen concen- trations were depleted at less than 20-foot depths. These stratified conditions were broken at least 4 tlies during each of these two 185 summers as a result of severe rain-wind storms. During first half of September of each of these years, a drop of approximately 20 C in surface water temperatures has produced an overturn in the entire lake with a complete mixing of adequate dissolved oxygen for fish life at all depths. Even though many regions of the lake were un- suitable for occupancy by fish during these hot, stratified periods, sufficient areas of aerated waters (approximately 600,000 acre-feet) were available for fish habitation. Throughout 1967 the weather was abnormally cool and surface water temperatures seldom exceeded 28 0 C and bottom waters at 75+ foot depths were approximately 5* cooler. While the dissolved oxygen concentrations in surface waters never exceeded saturation even under these cooler conditions, the dissolved oxygen concentrations even at 85-foot depths was never completely depleted. These semi- stratified conditions were disrupted at 10-to 14-day intervals by cool, rainy weather conditions. Throughout the three summers this lake has been under observa- tion, water temperatures and dissolved oxygen concentrations have been in a constant state of change both in relation to time and to location within the reservoir. In a series of dye studies conducted during mid-summer of 1966 it was demonstrated that even under hot weather conditions the waters in upper portions (region of impoundment contained within old river channel) were completely mixed even in areas with water depths of 40 feet. In deep water (70+_foot depths) areas under extreme stratified conditions, a dye injection into the 10-foot strata of bottom waters 186 in old river channel moved at a rate of 0.08 mph over a 12.mile stretch of river channel and did not mix with overlying waters through- out this area. One deep-water dye injection into the river channel in on area immediately downstream from a dual bridge installation at Eufaula, Alabama, moved downstream in a 10-foot strata for 24 hours, but then reversed its movements and during the next 96 hours moved for a distance of 2.5 miles upstream. This demonstrated that partial ob- struction within a reservoir may produce peculiar flow patterns that could enhance nuisance conditions produced by various pollutants. In fact it could simulate the piston-type currents characteristic of estuaries that are subjected to tidal action. This condition should be recognized and considered in designing bridges and jetties for new reservoirs. A total of 15 elements in raw lake waters were routinely determined. These are all in the essential element category for plant growth. The principal nutrient elements nitrogen, phosphorus, and potassium were each present in sufficient quantities (3 year overages, ppm N = .242, P = .037, K = 1.73) to have supported on abundant growth of phytoplankton. However, production of such a growth was never attained throughout the 3 year period of this re- search. This fact is verified by on averaged total carbon content in row waters of 11.6 ppm and it never exceeded 23.5 ppm even in on area where inadequately treated domestic sewage was present. Thus, the production of undesirable blooms of phytoplankton on Lake Eufoulo involves other factors in addition to on adequate, available supply 187 of nitrogen, phosphorus, and potassium. In the case of total carbon content (11.6 ppm), the carbonate carbon (=CO 3 ), as estimated by total alkalinity determinations, accounted for an averaged 2.43 ppm carbon. Of the remaining 9.2 ppm of carbon, that portion which could be readily degraded into CO 2 as determined by 5-day B.O.D. tests never exceeded 1.0 ppm carbon. Thus, Lake Eufaula with all of its multi-sources of agricultural, domestic, and industrial pollution did not have an organic carbon pollution problem during this 3-year period. The soluble calcium content of this reservoir averaged 4.2 ppm over the 3-year period. The calcium content in 1965 and 1966 averaged 4.6 ppm but in 1967 it dropped to 3.4 ppm. The cause of this drop is unknown, but all data indicate that these waters were calcium poor to the extent that the lack of this element might be a limiting factor in aquatic life development in this reservoir. The soluble magnesium, on the otherhand, remained fairly constant around the average of 1.2 ppm over the 3-year period. This quantity of magnesium appears sufficient to adequately support aquatic life. The soluble sodium content averaged 5.1 ppm, and varied slightly around this value for the 3-year period. The total iron and manganese concentrations in raw waters, averaged .428 and .097 ppm respectively. Concentrations of each element varied considerably from these values depending upon turbidity, stratification, and phytoplankton production. Values for iron concentrations were increased by turbidity and stratification 188 (dissolved oxygen depletion). Values for manganese were decreased by turbidity, and increased by stratification and phytoplankton pro- duction. The copper concentrations inraw waters ranged from .001 to .63 ppm and the zinc concentrations in same water ranged from .001 to 1.25 ppm. Neither the source nor cause of this wide range of these two elements are known. Their presence in such large amounts in waters of Lake Eufaula and other impounded waters in its vicinity has caused concern in regards to their possible detrimental influence on aquatic life in these habitats. Ranges in concentrations of other minor elements in water samples were as follows: Strontium .001 to .03 ppm. Nickel .01 to .03 ppm. Chronium .001 to .03 ppm. Cobalt .001 to .005 ppm. Lead .001 to .04 ppm. In the case of each of the metallic elements, it was possible to remove as much as 2/3 of the indicated concentrations in raw waters by filtering the samples through an 8 l millipore filter. This indicates that a major portion of each of these metals was a constituent of either colloids or particles that were of sufficient size to be retained by this 8 p filter. Studies on composition of suspended matter in reservoir waters were confined to 1967 since a usable technique for separation of the 189 suspended matter from raw waters had to be devised. The technique adopted for these studies employed an 8 p pore-size Millipore filter, an aqua-regia extraction procedure, and analyses by an atomic absorption spectrophotometer. Comparative data on suspended matter in commercial catfish ponds and in reservoir and tributary creek waters were collected during summer of 1967. In each of these habitats the quantity of suspended matter, that was composed of microscopic plant material, increased as the summer progressed. The total carbon content of these suspended matter samples also increased, but not in direct proportion to quantity of suspended matter in all cases. This discrepancy in quantity of suspended matter and total carbon content is believed to have been due to increased bacterial populations which were not retained by the 8 p pore-size filter and thus were not present in carbon analyses. The mineral contents of these suspended matter samples were higher in the early summer and generally decreased as the summer progressed. The rate of decrease of such elements as calcium, magnesium and sodium appeared to be closely associated with phytoplankton pulses, ,i.e. new plant growths. In the.case of iron, manganese, copper, zinc, and potassium the changes in content of suspended matter seemed to be associated with depletion of dissolved oxygen in bottom waters. Thus, it is suspected that most of these elements might have been present as suspended colloids and were retained as such by the filters. More sophisticated equipment and techniques will have to be employed to answer this question. From all data accumulated on composition of suspended matter 190 it appears that phytoplankton can assimulate large amounts of certain metals in their normal metabolism, and that as the summer progresses these phytoplankton tend to change their chemical composi- tion and acquire a composition characteristic of an aging terrestial plant. However, until a method of separating organic and colloidal suspended matter is devised, the above statements must be considered as a conjecture on what actually happens. These data on suspended matter compositions are extremely valuable since they represent that portion of raw surface waters which have here-to-fore been disregarded in routine laboratory analyses of filtered water samples. If the chemical content of natural surface waters are to be utilized in the establishment of water quality criteria by State and Federal agencies these chemical con- tents of suspended matter must be considered as a portion of surface water composition. Sampling of bottom soils in Lake Eufaula was initiated in 1965, and was continued through 1966 and 1967. During 1965 and 1966 deep water samples were collected with a core sampler. In 1967 only the dewatered edge of lake was sampled with this apparatus. A new bottom sampler was designed and built by Project Leader in 1967. This sampler collects that portion of the bottom sediment that lies between the solid bottom soil and the overlying water. This has commonly been described as the interface area or zone. Since the materials which this sampler collects are semi-fluid in nature, they have been called hydrosol. This sampler was used to collect all underwater bottom samples during 1967. It was also used to collect 191 soil samples for herbicide residue analyses in aquatic weed control research. Residue analyses of soils collected by this sampler and those obtained by diving were identical. Thus, this sampler is collecting the soil surface area*which has here-to-fore been unavailable to surface operated samplers. All soil samples were dried and then extracted with a neutral cation exchange solution. Chemical analyses were made of the ex- tracted (exchanged) elements in this solution. In evaluating these data on exchangeable elements from bottom soils it is evident that sampling technique was a major factor in determining the quantity of an element or elements that could be recovered from a particular sample. In many cases the averaged quantity of an element recovered in the hydrosol samples exceeded the maximum quantity of that element recovered from any core sample. This does not indicate, however, that all necessary data on soil com- position studies in a reservoir could or should be obtained with a hydrosol sampler, for example, the marginal sampling can only be accomplished with a core sampler if one is to obtain reliable data on elements available to plants whose roots extend several inches be- neath the soil surface. Likewise, one should use the hydrosol sampler to determine those exchangeable elements that are currently being depositied or that could be used by various submersed plants, algae and floating plants. To understand the chemical complexities of any aquatic habitat requires a knowledge of the chemical composition of aquatic plants that occur in the environment. Since aquatic plant development on Lake Eufaula has been limited, sampling of other occupied areas, i.e. 192 Lake Seminole and various experimental ponds and pools, was carried out in an attempt to find the explanation for this lack of aquatic plant development. Only four aquatic plant species of any immediate concern were growing in Lake Eufaula during this study period. These plants were alligatorweed, giant cutgrass, smartweeds, and Paspalum fluitans. Of these four, only the first two were found in the other habitats under observation. Another aquatic species, waterwillow, was growing in Bartlett's Ferry Reservoir, which is immediately above, and in Lake Seminole, which is below, but none was found within Lake Eufaula. Chemical composition of alligatorweed from various environments indicated a wide range in composition of such elements as calcium, magnesium, iron, manganese, sodium, and phosphorus in apparently normal plants, but lush growth of this species seemingly was associated with an abundant supply of nitrogen and potassium. It was also apparent from a study of the habitat, as well as the com- position of the plant, that the nitrogen and potassium had to be supplied to the water roots and that the maintenance of an adequate concentration in the water medium was essential for lush growth. In Lake Eufaula it has been observed that alligatorweed was apparently seriously retauded each winter by the 5-foot draw-down, and that it required the first half of each summer for surviving plants to become reestablished to the extent that they were able to effectively absorb nutrients from the flowing waters. However, during latter part of July and through August and September these reinfestations produced plant growths that indicated a luxury supply of nutrients. 193 Chemical data on waterhyacinths from habitats with different nutrient levels indicated that this species possibly has a wide composition tolerance for such elements as calcium, magnesium, iron, manganese, phosphorus, and sodium, but to produce healthy plants, the available nutrient level must be higher than for all alligatorweed. Since this is a floating species, its nutrient requirements must be met by an ample concentration of all elements in the water. Eurasian milfoil is a newcomer to this section of United States. However, from the vast area it now occupies in certain sections of the Southeast, it is evident that certain habitats are suitable for its propagation. Data on chemical composition of plants from 2 infected areas and one from plastic pool provides evidence that this species has a high calcium requirement. In Lake Seminole, the only area presently infested with this species has a high calcium content in its waters (20+ ppm) and even though living propagules are floating into other areas of the lake, the plant has not become established any place where the calcium content is less than 20 ppm in the water. Since most aquatic plants are capable of absorbing large amounts of major and minor plant nutrients from the surrounding waters, they have a potential use as collectors or absorbers of various types of nutrient pollutants. Their use in this role only awaits an economical method of harvesting and utilizing such nutrient collectors. Rotenone sampling in 1965, 1966, and 1967 of the fish popula- tion in Lake Eufaula indicates that at least 29 species are present, 194 but that less than 5 percent (approximately 20 lb. per acre) of the total weight per acre could be classed as harvestable sizes and species for the sport fishermen. This population composition is typical of reservoirs in the southeastern region of United States. Fishing success, however, has been phenomenal for largemouth bass, and black and white crappie, and, sport fishermen have not complained of any decline in catch over this 3-year period. This is a bit unusual since catches by sport fishermen have generally started declining by the 4th year after impoundment (1967) in most reservoirs in this region. Since the principal interest of this study was to compare chemical composition of various life forms in this reservoir en- vironment, samples of 21 different species of fish were randomly collected by use of rotenone, electricity, and seining from Lakes Eufaula and Seminole and from various fish ponds within the vicinity of these lakes. Each fish used for analyses was measured and weighed, freeze-dried, ground, a sample ashed, the residue dissolved in a weak acid solution, and this solution analyzed by atomic absorption spectro- photometer. Comparative chemical composition data on two species, largemouth bass, and bluegill, from both Lakes Eufaula and Seminole and from experimental ponds have indicated an increase in calcium content of whole fish from the 2-inch group through the juvenile sizes (for each species) and then a decrease in calcium content in the adult sizes. It was also found that copper and zinc content within these 195 2 species was from 5 to 20 fold greater in reservoir fish than in experimental pond fish. Incidentally these pond fish were from habitats where copper sulfate had been applied for algae control, and indicates that the use of this algacide will not result in as much residue in fish as may be found in specimens from streams and reservoirs. Other heavy metals such as chromimum and lead were also more abundant in stream fish than in those removed from ponds. Some evidence on possible sources of some of these heavy metals is available, but further sampling of all species is needed to firmly establish these sources. Based upon the data accumulated thus far on this study of Lake Eufaula, the approximate relative abundance of some selected elements in water, suspended matter, hydrosol (soil), plants, and fish were as follows: Element Calcium Magnesium Iron ppm Monganese ppm Sodium ppm Potassium ppm Phosphorus ppm Copper ppm Zinc ppm Nitrogen ppm Carbon ppm Water (raw) 4.2 1.2 .4 .1 5.1 1.7 .04 .03 .06 .242 11.6 Suspended matter .13 .03 .40 .03 .17 .33 .107 .128 2.4 Hydrosc (dry wt. 1640 380 320 540 380 180 50 8 28 1965 23,430 l Plants (dry wt, 7100 6000 1575 530 5200 40000 1850 80 135 30,000 363,000 Fish (dry wt.) 35,000 2,000 150 35 2,500 7,000 38,000 105 131 98,000 412,000 m........ .... r. 196 In most cases the maximum concentration for any element listed above was 2 or more fold the given approximate quantity. Thus, more extensive sampling is needed to establish a better average and range of composition of these and other elements in the various portions of the aquatic environment in Lake Eufaula and its associated head and tail-waters. 197 APPENDIX TABLES Appendix Table 1-A Averaged temperature, dissolved oxygen concentration, pH, and resistivity of water a indicated locations and depths in upper region of Lake Eufaula for 1965, 1966, and 96 ITEMP . 0 C 1 65 66 _ 0.7..0*15-12 27.5- 0-129.6C 23.88 23.80 0129.00 21.74 201,28.95 ?1.92 23.80 OXYGEN PPM 6.40 6.25 6.78 5.83 6.26 6.60 p H 7.54 7.34 6- 6 6.02 7.77 7.33 7.43 6.73 6.98 6.51 6.80 7.26 7.21 5.27 6.90 6.40 6.53 7.28 7.20 OHMS/I M 3 15280 16125 17844 13300 19475 16617 15400 17075 17583 1387-5 17433 17067 6.5 705 6.4 7.4 7.2 18500 14630 22350 m013.10 26.99 25.5 30 9.03 24. 78 29.45 7.00 6.63 8.10 5.00 5.40 6.45 7.10 7.22 7.2 6.93 7.21 7.2 15467 17050 17200 15067 17832 18325 0 130.00 28.80 23.75 401 28.05 26.00 O 23.5 25.3 30't 21.25 25.0 0O30.10 26.25 25.14 20 1k8.83 23.99 23.86 40'p18.60 24.2.0 25.10 6.50 7.62 6.70 4.46 5.63 8.0 7.00 5.37 2.75 7.10 6.72 ".0 5.07 5.64 6.9 5.30 5.13 6.9 7.90 7.39 6.91 7.08 7.18 7.6 8.00 7.4 6.75 6.83 7.21 7.18 6.50 7.01 6.0 6.55 6.98 5.15 15300 16955 16440 19500 19450 18628 17083 14867 16850 16175 17054 18323 15750 17130 17400 16620 19000 15975 N- of 30.5 23.0 Appendix Table 1-B Averaged temperature, dissolved-oxygen concentration, pH, and resistivity-of water t n dicated locations and depths in middle region of Lake Eufaula for 1965, 1966, and 16 d' 31.50 27.75 25.90 ~o28.90 26.00 20.35 d' 26.02 27.62 26.50 20' 24.95 26.80 25.50 40' 24.55 26.58 25.43 60' 24.40 25.17 25.10 OXYGEN .PPM '65 '66 t7 7.10 6.72 7.00 5.07 5.64 6.90 5.30 5.13 6.90 8.71 8.65 2.05 4.10 pH '65 6.83 6.50 6.55 6.7 6.43 8.40 5.92 3.85 3.65 2.33 6.07 1.77 1.42 9.00 1.50 6.83 4.40 4.13 9.5 3.62 8.00 2.50 2.90 7.3 6.5 6.4 7.15 7.00 7.05 7.07 6.35 7.34 6.38 4.35 4.63 3.50 2.90 3.91 2.?5 2.30 3.10 3.56 6.0 7.42 7.95 .45 1.67 3.00 6.06 6.81 7.80 3.30 4.32 6.30 2.55 2.46 .4.07 2.54 1.82 2.86 '66 7.21 7.01 6.98 7.86 7.03 7.18 6.00 5.15 7.85 6.90 7.85 6.80 8.90 7.30 7.61 7.71 7.12 7.45 7.08 6.80 7.30 8.25 6.70 7.80 7.15 7.22 6.75 7.20 6.3 7.58 7.05 7.16 7.03 7.12 7.05 7.18 6.87 7.25 8.08 7.30 5.70 7.25 6.35 7.37 7.82 7.16 6.44 7.27 6.80 6.52 7.05 6.53 6.42 7.13 6.40 OHMS / CM 5 '65 '66 '67 16175 17054 18323 15750 17130 17400 1662 0 19000 15975 13900 19989 16150 14366 12740 16050 22000 17400 16000 15914 16633 16325 16700 15414 15566 16400 17933 16900 14500 13600 13600 12640 11600 18700 17185 18900 17866 18500 17633 16900 16128 15950 150~50 11900 17100 17166 15100 16616 15250 16075 16430 13150 12600 13500 15671 17050 162,!3 16414/ 17192 17266 16467 16292 17066 15600 16142 16666 TEMP. *C '65 '66 d' 30.10 26.25 20', 28.83 2'3.9 9 4d' 28.60 24.20 d' 28.43 20' 24.90 d' 2d' 40' 25 .14 23.88 25.10 27.00 2 5.60 28.0 27.9 ad 40' 60' 0 3d 25.00 22.00 29.06 27.17 27.90 25.40 27.61 27.66 '25.96 '26.58 24.58 0' 28.00 20' 26.67 4d' 26.17 0' 26.00 29.37 20' 25.0'0 25.48 40' 24.57 25.09 60' 25.90 25.50 26.50 24.50 26.00 26 .60 24.75 24.72 23.75 f-1 3o Appendix Table 1-C Averaged temperature,, dissolved oxygen concentration, pH-, and resistivity of water t n dicated locations and depths in lower region of Lake Eufaula for 1965, 1966, and 196 TEMP. *C '65 '66 '67 0' 26.02 27.6~'265 2d' 24.95 26.80 25.50 4d 24.55 26.58 25.43 60d 24.40 25.17 25.10 d0' 27.0 29.5 40' OXYGEN PPM X65 '66 67 6.06 6.81 3.30 4.32 2.55 2.46 2.54 1.82 ?5.00' 28.00 24.50 ?7.00 d1 31.5 28.61 26.85 EdJ 28.35 26.27 24.75 4dj 27.75 95.97 24.35 6d' 27.20 25.62 23.75 8.15 1.95 .42 .20 65 '66 67 7.80 6.30 4.07 2.86 6.5 8.0 3.0 2.5 7.0 6.5 2.6 1.5 6.58 8.60 3.45 2.97 2.55 1.57 1.88 1.32 OHMS /CM '65 '6 67 7.37 7.82 7.16 15671 17050 16833 6.44 7.27 6.80 16414 17192 17266 6.52 7.05 6.53 16467 16292 17066 6.42 7.13 6.40 15600 16142 16666 8.2 7.2 7.1 6.5 8.7 8.5 7.2 6.5 18750 17300 20800 19700 18500 16900 7300 15500 7.9! 7.82 8.35 16900 16855 16400 7.00 7.22 6.55 15600 17138 16150 6.8C 7.11 6.50 15800 16570 15700 6.85 7.10 6.80 15300 15500 16900 401 0'd 29.44 29.31 20' 28.35 28.12 40d 26.90 27.30 60I25.88 25.78 8026.17 26. 59 27.40 25.75 27.75 25.60 24.5 24.5 7.12 4.94 2.80 1.62 1.91 7.11 5.87 4.02 3.12 1.16 6.37 4.50 6.50 6.55 8.15 6.32 2.80 1.12 7.84 7.11 6.78 6.47 6.60 8.18 7.82 7.43 7.31 7.19 7.15 16144 6.95 15800 6.40 16600 13966 6.35 17957 0 0 19050 21400 17855 17200 18644 17250 18189 17100 17814 16000 15500 Appendix Table 2-A Averaged calcium,:magnesium, potassium, and sodium concentrations in water at i.ndicte locations and depths in upper region of'Lake Eufaula for 1965, 1966, and 1967 CALCIUM PPM '65 '66 '67- 014.46 4.40 3.42 o-14."32 4.40 3.08 701 3.49 5.0 2.91 2'9.18 4.98 2.69 -0'14.92 4.80 6.0 0 4.03 4 57 2.76 30:13.89 4.97 1.00 4.50 4.45 4.10 5.0 4.54 4.56 4.73 2.62 3.71 3.00 4.57 3.03 4.35 3.45 MAGNESIUM PPM 65 '66 '67 1.21 .99 1.22 1.18 .95 1.17 1.23 1.22 .1.13 1.26 1.19 1.13 1.55 1.41 1.01 1.28 1.17 1.13 1.34 1.21 1.20 1.34 1.17 - 1.13 - 1.09 - 1.20 1.27 1.13 1.20 1.11 1.32 1.13 POTASSIUM PPM 65 '66 '67 1.90 2.28 1.64 1.95 1.69 1.79 1.69 1.94 1.53 2.18 1.76 1.75 1.0 3.2 1.22 1.76 1.96 1.61 1.73 2.04 1.85 1.16 1.17 1.13 1.07 .93 1.16 .80 1.74 1.65 - 1.89 - 1.96 - 1.81 1.91 .2.07 1.96 1.95 1.77 2.10 SODIUM PPM 65 '66 '6? 6.68 5.8 5.11 8.00 4.78 5.33 6.33 4.86 6.32 7.26 4.43 5.05 2.0 8.22 2.18 6.53 5.63 6.54 6.22 4.98 5.60 1.79 1.80 1.51 1 .44 2.07 .54 2.71 5.5 5.17 - .5.06 - 3.70 - 4.29 5.9 4.4 5.74 4.36 5.37 4.49 5.05 5.28 5.48 4.03 3.95 4.75 5.12 0 I-a Appendix Table 2-B Averaged calcium, magnesium, potassium, and sodium concentration .s in water at indicte locations and depths in middle region of Lake Eufaula for 1965, 1966, and 196-7 MAGNESIUM PPM '65 %6 t 1.27 1.13 .93 1.20 1.11 1.16 1.32 1.13 .80 1.18 .96 1.18 1.17 1.03 1.14 1.43 1.30 1.15 lUM PPMW 166 '67 4.54 3.03 4.56 4.35 4.73 3.45 7.54 3.52 8.54 2.80 3.80 2.80 3.35 4.15 4.29 3.21 3.92 3 .50 4.32 4.06 2.70 POTASSIUM PPM '65 '66 '67 1.91 2.07 2.07 1.96 1.95 .54 1.77 2.10 2.71 2.65 1.67 1.45 2.15 1.60 1.52 1.75 1.70 .95 1.02 1.73 1.25 1.71 1.15 1.85 1.86 1.28 1.04 1.01 SODIUM PPM '65 '6 Ii 5.9 4.4 3.95 5.74 4.36 4.75 5.37 4.49 5.12 6.5 3.32 5.40 6.66 3.19 5.55 4.50 5.70 4.48 4.48 4.99 5.87 4.81 5.37 5.39 4.04 5.83 5.80 4.11 ,' 2.60 10.36 4.48 20] 6.20 11.20 5.70 4c16.80 12.23 7.60 13.84 4.42 2.76 :2d'3.55 4.68 3.05 4013.93 4.62 4.35 60,3.95 5.45 2.62 d15.03 4.3 4.62 3Y6.55 7.52 11.62 02.94 4.68 3.97 2d 3.60 4.85 3.68 4d 4.24 4.98 3.83 6050 5.54 3.60 1.25 1.20 1.04 1.18 1.17 1.00 1.18 1.20 1.05 1.45 1.40 1.35 1.55 1.15 1.15 1.18 1.28 1.08 1.67 1.11 1.22 1.62 1.015 1.18 1.62 1.29 1.20 1.40 1.43 1.40 1.45 1.20 1.17 1.19 1.15 1.20 1.30 1.22 1.20 2.00 1.66 1.41 2.10 1.78 .91 1.90 1.53 2.02 1.80 2.02 1.31 1.88 2.13 1.50 1.73 2.10 1.11 1.86 2.01 1.56 1.65 1.56 1.68 1.80 1.85 1.67 1.50 2.02 1.40 1.60 1.97 1.41 1.90 2.06 1.56 1.90 2.06 1.53 6.0 5.75 5.50 3.68 4.07 3.34 4.77 3.15 2.40 4.0 4.83 5.53 3.92 5.04 4.47 4.16 4.50 4.72 4.25 4.34 4.96 7.5 3.37 4.68 8.8 3.46 4.36 4.0 4.0 4.0 4.0 4.91 5.46 4.88 5.48 4.84 5.26 4.50 5.17 N) 0 1.17 1.25 1.10 1.13 1.30 1.06 1.23 1.06 1.25 1.11 1.08 1.05 1.16 4.02 3.51 Appendix Table 2-C Averaged calcium, magnesium, potassium, and sodium concentrations in wa ter at i*ndicate locations and depths in lower region of Lake Eufaula for 1965, 1966, and 1967 MAGNESIUM PPM '65 '66 '67 1.40 1.20 1.17 1.43 1.19 1.15 1.40 1.20 1.30 1.45 1.22 1.21 1.17 1.13 1.25 .82 .98 1.18 .945 1.10 1.50 1.25 1.28 1.56 1.22 1.31 1.50 1.27 1.40 1.50 1.25 1.10 OPIUM PPM '66 '67 4.68 3.97 4.85 3.68 4.98 3.83 5.54 3.60 3.95 2.6 6.63 4.6 4.5 3.4 12.67 4.6 4.74 3.40 4.94 3.77 4.57 3.72 5.00 4.32 4.77 4.45 1.28 1.12 1.17 1.32 1.10 1.17 1.31 1.12 1.18 1.21 1.13 1.28 1.12 1.26 POTASSIUM PPM t5 t6 '67r 1.8 2.02 1.40 1.8 1.97 1.41 1.75 1.98 1.56 1.60 2.06 1.53 1.34 1.40 1.35 1.05 1.93 1.30 1.87 1.30 1.63 1.90 1.45 1.57 2.18 1.55 1.67 1.79 1.47 1.55 2.16 1.05 .77 .50 1.57 1.72 1.34 1.69 1.72 1.30 1.56 1.70 1.40 1.82 1.78 1.55 1.54 2.0 SODIUM PPM t5 '66 4.91 5.46 4.0 4.88 5.40 4.0 4.84 5.26 4.0 4.50 5.17 3.64 7.0 3.01 3.2 2.98 6.0 2.18 4.65 7.5 4.62 7.5 4.28 7.0 4.46 6.5 4.90 5.95 5.95 5.49 4.19. 2.78 1.42 6.59 4.36 4.72 8.23 3.93 4.68- 8.09 3.93 4.50 1.77 4.21 5.88 3.52 5.25 .87 .68 0 Appendix Table 3-A Averaged turbidity, alkalinity, and EDTA hardness concentrations in water at indicated locations and depths in upper region of Lake Eufaula for 1965, 1966, and(96 ALKALINITY PPM C *65 U66 t7 28.5 21.0 17.98 32.02 17.9 22.61 C0 3 EDTA HARD. PPM C CO 3 '65 '66 '67 17.3 14.41 13.0 20.56 14.80 13.25 14.57 13.95 16.02 18.78 18.12 15.4 14.56 12.75 20.18 16.83 29.51 18.02 15.83 15.29 13.88 13.00 24.0 11.50 24.8 23.7 15.0 20.5 14.7 027.3 15.86 9.83 3034.2 20.07 16.50 8.43 13.26- 8.0 20.0 15.96 15.45 7.0 21.0 07.0 20.85 16.0 20'2 2.25 28.11 40'2 5.0 30.68- 20.75 23.87 17.5 16.67 23.17 17.3 16.87 24.50 18.33 19.16 17.29 16.43 20.0 24.58 15.83 16.88 22.12 18.0 17.70 23.89 16.13 17.50 24.26 16.81 19.44 15.8 14.75 13.0 15.66 14.50 13.25 16.1 15.35 13.10 15.58 13.62 15.0 13.0 14.33 13.0 15.23 14.55 13.6 15.71 13.77 15.25 15.14 14.68 14.0 TURBIDITY 65 '66 o'j 2 4. 6 9.07 ol 10. 10.84 JTU '67 16.33 16.6 L'.J 0 Appendix Table 3-B Averaged turbidity, alkalinity, and EDTA hardness concentrations in wa ter at in- dicated locations and depths in middle region of Lake Eufaula for 1965, 1966, and 16 TURBIDITY JTU '6 5 '6 6 6 7 d27.0 20.85 16.0 2d 22.25 28.11 4d 25.0 30.68 20.75 ALKALINITY t5 '6 22.12 18.0 23.89 16.13 24.26 16.81 PPM C C0 3 17.70 17.50 19.44 EDTA 15.23 15.71 15.14 HIARDN SS FPM C CO 3 '66 67 14.55 13.6 13.77 15.25 14.68 14.0 12.06 7.5 22.10 17.0 29.70 19.98 24.37 28.10 24.05 16.87 21.5 21.33 22.05 6.4 12.0 1 4.25 8.0 2 3.33 10.75 22.81 22.75 13.33 9.3 23.3 5.67 12.15 15.0 8.3 19.2 27.5 13.33 12.4 26.41 15.33 22.10 10.50 25.33 20.33 20.00 17.0 13.0 20.06 20.6 12.0 15.0 15.0 15.75 16.25 22.5 30.4 28.2 30.7 23.02 21.55 25.90 30.60 17.50 17.08 17.27 18.75 18.13 16.56 18.75 16.25 18.25 23. 7 20.25 27.74 20.0 30.6 17.92 18.5 16.16 18.33 17.00 20.0 15.15 18.75 7.5 5.16 33.75 16.56 18.75 46.0 40.5 31.00 23.13 25.0 0 20.3 7.25 11.'33 20 27.50 10.83 12.33 4d 33.25 12.81 13.33 6&' 31.0 15.95 13.66 18.08 18.75 17.91 21.46 17.91 17.91 21.40 18.11 17.50 25.10 20.55 17.50 19.7 21.6 21.0 18.0 17.97 14.47 17.50 14.94 13.0 14.45 13.0 15.13 18.38 12.75 12.0 12.5 22.6 20.0 28.6 16.0 3 2.8 33.5 14.68 13.3 14.53 14.75 14.74 17.66 14.33 23.75 15.25 14.0 27.8 15.25 22.0 14.38 13.95 13.25 14.50 14.92 13.00 16.50 21.98132 17.0 17.16 13.75 0 Appendix Table 3-C Averaged turbidity, alkalinity, and EDTA hardness indicated locations and'depths in lower region of TURBIDITY '65 '66 0'20.3 7.25 20' 27.5 10.83 4d3.512.81 6di 31. 0 15.95 41 32.7 4d] JTU '67 11.33. 12.33 13-.33 13.66 5.0 50.0 concentrationsin water at Lake Eufaula f or 1965, 1966, and 1967 A LKALINITY '65 66 18.08 18.75 21.46 17.91 21.40 18.11 25.1.0 20.55 17.5 19.16 6.0 4.0 9.75 6.0 PPM C CO 3 '67 17.91 17.*91 17.50 17.50 17.5 16.25 EDTA '65 14.38 14.50 16.50 17.00 17.5 17.5 44.37 21.25 HARDNE~SS PPM C CO 3 ' 66 '67 13.95 13.25 14.92 13.00 21.98 13.25 17.16 13.75 15.0 14.0 21.66 18.0 17.0 15.0 48.25 20.0 0'd 13.5 4.95 5.25 2of 2 6. 0 8.73 7.25 435.0 10.32 8.50 6d1 44.0 10.22 11.25 40' 9.75 25.5 d' 9.45 4.5 1.85 2d 10.8 3.64 2.25 401 11.5 4.03 5.0 6d 27.1 6.25 ad 49.1 10.38 6.0 29.06 18.87 18.75 19.53 18.27 19.37 21.43 19.03 19.37 20.87 21.25 20.0 18.41 16.87 22.18 19.00 19.37 21.93 17.66 18.75. 25.46 19.11 18.75 25.70 19.29 29.42 23.50 18.75 14.33 15.11 15.0 15.06 15.59 14.5 16.06 15.50 15.0 16.70 17.28 17.5 16.0 16-75 17.21 15.30 14.5 17.21 15.56 14.0 18.43 14.93 15.0 20.37 15.94 21.56 17.90 16.5 w% 0 Appendix Table 4-A Averaged iron, manganese, zinc, and copper concentrations in water at indicated lcain and depths in upper region of Lake Eufaula for 1965, 1966, and 1967 IRON PPM 65 '66 '67 djl .13 .366 .532 -. 122 .453 .540 ol .18 .69 .44 20' .10 .72 .873 -oj.37 .43 .73 01.09 .62 .236 301.083 .73 .86 01.10 .44 .623 401- .73 .750 o011 .062 .316 3d .523 .777 d.129 .79 .607 -20' A20 .98 .08 4d0.151 .88 .612 MANGANESE PPM '65 '6a6 '67 .036 .030 .009 .061. .130 .045 .025 .075 .021 .038 .095 .052 .058 .023 .0 .030 .140 .012 .022 .141 .040 .005 .030 .032 - .056 .043 - .022 .021 - .027 .009 .020 .07 .022 .038 .11 .024 .021 .26 .039 ZINC PPM 65 '66 !67 .006 .085 .044 .002 .138 .042 .. 005 044 .036 .007 .066 .039 .002 .081 .012 .011 .065 .02 .015 .043 .062 .065 .035 .032 - .061 .035 - .015 .116 - .018 .031 .011 .063 .067 .007 .070 .050 .007 .073 .034 COPPER PPM 65 '66 '67 .004 .005 .012 .007 .006 .015 .002 .022 .019 .007 .022 .019 .006 .001 .005 .009 .003 .06 .047 .011 .002 .005 .004 .018 - .003 .006 - - .243 - - .020 ,017 .006 .110 .016 .006 .010 .010 .009 .035 N Appendix Table 4-B Averaged iron, manganese, zinc, and copper concentrations in water at indicated lo- cations and depths in middle region of Lake Eufaula for 1965, 1966, and 1967 IRON PPM '65 '66 '67 d.129g .79 .607 2-0. 12 0 .98 .08 40-.151 .88 .612 d. 07 1.128 .16 ad.09 2.41 .955. 0.005 - .83 4d'. 016 0' 30' di 20d 4d' 60' cd 30 MANGANESE PPM '65 t6 '67 .020 .-07 .022 .038 .11 .024 .01 .26 .039 .05 .025 .012 .07 .154 .034 005 .005 .027 .09 .24 .64 .313 1.04 .280 1.01 .500 1.17 ZINC PPM '65 '66 67 .011 .063 .067 .008 .070 .050 .007 .073 .034 COPPER PPM '65 '66 t7 .017 .06 .110 .025 .006 .1 .015 .009 .035 .018 .051 .033 .006 .003 .033 .012 .324 .055 .006 -. 006- .032 .005 .020 .013 .07 .020 .04 .023 .75 .040 .09 .161 .485 .071 .102 .129 .086 .015 043 .02 .043 .045 .049 .050 .030 .090 .137 .013 .016 .010 .005 .013 .004 .016 .001 .009 .007 .083 .079 0 .130 .372 .355 20. 127 1.632 .400 40f.127 2.128 2.200 df.177 .79 .338 20'.285 .98 .396 4d.315 1.25 .365 6d.528 1.38 .750 0d.270 .73 .198 30.320 1.91 .956 cd.214 .33 .403 20'. 175 .59 .443 40. 150 .69 .563 6d.187 .97 .633 .073 .021 .028 .070 .043 .047 .070 .049 .132 .025 .10 .014 .008 .05 .049 .007 .265 .107 .008 .25 .091 .001 .013 .015 .103 4.705 .036 .005 .05 .026 .060 .10 .023 .032 .20 .046 .340 .63 .072 .018 .067 .045 .014 .132 .033 .014 .010 .055 .029 .027 .038 .021 .020 .150 .055 .019 .008 .009 .017 .009 .013 .013 .009 .005 .018 .050 .066 .100 .083 .048 .687 .072 .020 .062 .075 .015 .033 .053 .028 .141 .050 .085 .046 .060 .068 .080 106 .007 .132 .007 .251 .010 .280 .007 .015 .005 .009 .028 .004 .001 .020 .008 .012 .010 .009 .007 .036 .005 .041 .005 .084 .006 .066 0V 00 Appendix Table 4-C Averaged iron, manganese, zinc,, and copper concentrations in water at indicated lo- cations and depths in lower region of Lake Eufaula for 1965, 1966, and 1967 IRON PPM '65 '66 '67 0.214 .33 .4 03 201 .175 .59 .443 461.150 .69 .563 601.187 .97 .633 40] 401 0' .05 20 .16 40' .162 60' .097 40! .37 .20 1.653 3.45 .30 .05 .725 .15 .32 .165 .23 .20 .52 .30 .57 .40 MANGANESE PPM '65 '66 '67 .005 .05 .026 .060 .10 .023 .032 .20 .046 .340 .63 .072 1.002 .020 .233 .040 .04 .01 .007 .02 .03 .08 .02 .05 .02 .23 .03 .22 .857. 2.40 0.07 .055 .05 20P'.08 .17 .045 40' .12 .17 .111 .29 .55 60' .26 1.290 .175 80co .010 .025 .06 .105 .057 .150 .06 .02 .012 .045 *.11 .011 .057 .06 .038 .240 .23 .067 .95 .05 ZINC PPM '65 66 67 .015 .033 .060 .053 .078 .068 .141 .050 .080 .085 .046..106 .37 .022 .111 .030 .185 .03 .132 .03 .040 .046 .641 .028 .024 .122 .037 .064 .113 .022 .025 .061 .041 .037 .03 .016 .15 027 .027 .233 .014 .031 .099 .02F .028 .012 .026 .127 COPPER PPM 65 '66 67 .007 .036 .012 .005 .041 .010 .005 U84 .009 .006 .066 .005 .015 .004 .015 .010 .012 .010 .010 .002 .003 .062 .004 .052 .005 .003 .061 .002 .006 .081 .007 .011, .009 .001 .122 .005 .001 .262 .058 .001 .111 .007 .001 - .007 .001 .085 0 Appendix Table 5-A Averaged nitrogen,. phosphorus, total carbon, and carbon dioxide-free carbon concenta tions in water at indicated locations and depths in upper region of Lake Eufaulafo195 1966, and 1967 NITROGEN PPM 65 '66 '67 = 01205 .16 .25 01.485 .31 .15 0'1 .22 .177 .21 20' .306 .165 .145 0'j.22 -- 1.090 50,f.186 0' .060 40' 0'.2 20.31 4di9 .213 .17 .145. .15 .100 .195 .170 .40 165 .189 .201 .45 .265 .666 .265 .179 .055 .131 PHOSPHORUS PPM '65 ',66 '6a7 .025 .002 .. 06 .050 .013 .066 .020 .050 .098 .033 .032 .050 .030 .001 .017 .022 .010 .069 .077 .006 .117 .013 .016 - .025 .007 .011 .01 .013 .054 .023 .014 .028 .076 .111 .046 .057 .077 .067 TOTAL CARBON PPM 65 '66 '67 11.8 13.95 10.05 17.0 .11.4 8.54 18.0 9.83 10.0 13.25 9.75 10.95 - 9.30 8.5 15.32 11.78 9.05 16.6 10.75 9.40 - 11.88 - 11.24 12.5 10. 93 11.6 10.17 9.91 11.07 9.75 15.50 CO -FREE CARBON PPM 65 66 '67 - - 5.3 - - 4.42 - - 4.48 -02 - 4.03 5.0 4.65 5.50 11.46 10.02 10.53 9.6 9.77 12.0 12.0 - 6.32 - 4.45 4.83 4.45 - 5.93 - 7.2 - 6.5 0 Appendix Table 5-B Averaged nitrogen, phosphorus, total carbon, and carbon, dioxide-free carbon concentain in water at indicated locations and depths in middle region of Lake Eufaula f or 1965 1966, and.1967 NITROGEN p M t5 156 V7 d .240 .165 .179 20' .310 .189 .055 40 .395 .201 ..131 d .12C .118 .235 3.370 .140 .320 20 4d' 30 2d' 40 PHOSPHORUS PPM '6 5 66 67 .010 .013 .077 .054 .. 023 .014' .028 .067 .020 .007 .16 .033 .004 .099 .210 .360 .190 .217 .283 .209 .360 342 .010 .011 .011 60' .138 .236 0' 30' .315 .273 0'.140 .352 .240 20.180 .398 .450 .0*220 .138 .680 0'.08 20'-.17 40'24 60' .030 .030 .030 .002 .025 .022 .020 .173 .357 .226 .325 .189 1.560 .279 .465 0 .136 .096 .283 36. 146 .136 .340 0? 2d' 4d 60' .287 .366 .292 .376 .370 .330 .394 .350 .029 .026 .060 .056 .005 1.072 .036 .057 .004 .028 .004 .047 .011 .135 .005 .080 .010 .111 .009 .052 .014 .123 TOTAL CARBON PPM '6 5 1 '67 9.91 11.07 12.00 9.75 15.50 12.00 11.90 10.80 15.65 11.55 9.00 Q9 10.85 9.60 9.30 10. 80 10.15 10.80 15.13 10.55 18.58 11.75 19.30 23.70 11.0 11.18 9.60 12.5 11.57 10.20 15.15, 11.72 10.30 10.0 13.22 11.30 .070 .010 .046 21.0 11.07 11.05 .066 .003 .081 19.67 14.60 15.00 .01 .008 .060 .01 .005 .068 .006 .. 08 .065 .106 9.5 12.42 9.80 12.3 12.03 9.56 13.53 1276 7.06 13.36 13.60 9.93 CO FREE CARBON PPM 65 '66 67 5.93 7.20 6.50 4.90 4.15, 5.50 5.50 5.60 6.00 4.90 6.27 8.50 6.50 6.65 7.85 14. 80 5.60 5.75 5.83 7.63 8.00 11.00 6.66 6.06 6.06 5.26 N~ I-a N- Appendix Table 5-C Averaged nitrogen, phosphorus, total earbon, and carbon dioxide-free carbon concen in water at indicated locations and depths in lower region of Lake Eufaula for 195M 96 and 1967 0.206 .169 .140 2d .347 .233 .150 40' .364 .245 .190 6dJ .448 .380 ad .409 .379 .210 PHOSPHORUS PPM '65 '66 '67 .01 .008 .06 .01 .005 .068 .006 .08 .065 .106 .001 .041 .001 .090 .01 .041 .05 .041 .05 .06 .05 .05 .005 .046 .003 .052 .003 .072 .005 .064 .045 .057 .032 .042 .032 .035 .033 .001 .057 .001 .041 .001 .048 .001 .002 .049 NITROGEN '65 1'66 0' .287 2d .292 40'0 60' CO 2 FREE CARBON PPM '65 '66 '7 6.06 6.06 5.26 8.1 13.8 7.0 7.0 PPM 67 .366 .376 .330 .350 TOTAL CARBON PPM '65 66 67 9.5 12.42 9. 12.3 12.03 9.56 13.53 12.76 7.06 13.36 13.60 9.93 11.0 11.8 11.65 19.0 11.0 11.7 20.0 16.3 6.0 12.0 15.00 9.0 11.55 9.75 14.0 11.97 9.90 11.0 13.50 10.00 11.75 14.00 10.15 11.35 9.50 13.65 11.51 9.70 13.45 11.11 10.50 11.86 13.14 9.85 13.64 10.50 5.75 4.2 3.8 4.15 5.82 6.45 5.25 5.25 5.53 4.5 N) N) .468 .190 .125 .200 .048 .250 .178 .420 4d1 40] 0 .136 20' .159 40' "112 6'.118 .223 .278 .290 .401 .260 .190 .190 .305 .315 .225 4d1 Appendix Table 6 Averaged monthly inflow and outflow, in cfs., for Lake Eufaula during period April193 Novemtber 1967. Courtesy: U.S. Army-Corps of Engineers District, Mobile Year Jan. 1963 1964 1965 1966 1967 19493 14465 1478 5 16748 Feb. 18026 19456 27050 13186 Mar. Apr. 29120 19219 27648 9363 8325 42125 12258 9998 5533 May 11959 21748 6320 14452 7565 June Inf low 6969 8369 7316 8333 July 8845 10222 6130 4930 9003 Aug . 5655 10056 5010 6257 9296 In- Sept. Oct. Nov. Dec. f low 3704 5682 4116 4592 8787 3606 15710 6404 7218 5660 4811 9192 3856 9157 9231. 8939 17164 5415 9057. Outf low 7738. 6552 6145 10215 8618 4874 7817 5300 7736 9915 1963 1964 1965 1966 1967 19120 13925 14155 18272 18211 19533 2608 6 13336 28768 18665 2843 2 93 57 10791 39471 14290 8607 5057 11397 22265 5637 12845 5566 7077 17140 9251 11872 9337 6894 17105 9300 11702 9346 5281 10379 3290 6933 8138 3857 5989 4699 4976 9835 3297 16554 6445 5677 6652 8775 18182 6316 8702 4355 5325 10895 214 Appendix Table 7 Pond Seepage and Pond Evaporation Losses in the Piedmont1 Month January February March April May June July August September October November December Seepage per acre pond Evaporation an I Loss Combined Loss Acre -Inches 6.7 5,9 6.6 6.6 7.0 7. 2 7*7 8.5 10.5 11.7 10.0 7.1 Total 95.5' 46.4 141.9 1. Calculated from "Hydrology of a small area near Auburn, Alabama", by D.A. Parsons, U.S.D.A. Soil Conservation Service and Alabama Agricultural Experiment Station Coop. S.C.S,-TP-85, 40 pp. (Records for 1947) Inches 1.4 1. 9 2.7 4.1 5.9 6.5 5.9 5.9 4.7 3.7 2.4 1.3 8.1 7.8 9.3 10.7 12.9 13.7 1L3.*6 14.4 15.2 15.4 12.4 8.4 215 Appendix Table 8 Spectrographic Analyses, expressed as ppb concentrations, of 1 Apalachicola river waters, collected at Blountstown, Florida Collection dates Element 12/17/58 3/30/59 8/24/59 9/29/59 Ag .11 .058 .098 .071 Al 73 2550 173 135 B 5 11 5.5 5.6 Ba 42 21 29 26 Be .058 Co .75 Cr 2.2 2.2 6.9 7.8 Cs Cu 2.1 7.0 51 6.2 Fe 96 1220 Ge Li .096 .70 .075 .12 Mn 5 25 20 4 Mo 0 .17 .46 .62 Ni 4.6 2.6 23 34 P 0 58 0 0 Pb 6.2 2.1 3.6 2.7 Rb 1.0 2.1 .75 2.1 Si Sn 1.3 Sr 34 7.5 28 25 Ti .8 99 8.3 6.9 V 2.2 0 0 Zn 0 0 0 0 Zr CFS 11000 54000 11900 9030 1. Source: Durum, W. H. Occurrence of trace elements in water. Proc. Conf. on Physiological Aspects of Water Quality. U.S. Public Health Service, Wash., D. C. pp. 51-66. LITERATURE CITED Hutchinson, G. Evelyn A treatise on limnology. Vol. I (Geography, physics, and chemistry). John Wiley and Sons, Inc., 1015 pp. 1957. A treatise on limnology, Vol. II (Introduction to lake biology and the limnoplankton). John Wiley and Sons, Inc. 1115 pp. 1967. 7 f