TPWD 1964 F-7-R-12 #940: Job Completion Report: Fisheries Investigations and Surveys of the Waters of Region I-A, Job No. D-3 Limnological and Game Fish Problems, Investigation on Buffalo Spri

--- Page 1 --- JOB COMPLETION REPORT As required by FEDERAL AID IN FISHERIES RESTORATION ACT TEXAS Federal Aid Project No. F-7-R-12 Fisheries Investigations and Surveys of the Waters of Region I-A Job No. D-3 Limnological and Game Fish Problems Investigation on Buffalo Springs Lake Project Co-Leader: George G. Henderson, Jr. J. Weldon Watson Executive Director Parks and Wildlife Department Austin, Texas Marion Toole Eugene A. Walker D-J Coordinator Assistant Director for Wildlife August 9, 1965 --- Page 2 --- ABSTRACT In 10 months of 1964, 39,085 fishermen paid to fish at Buffalo Springs Lake near Lubbock. Season passes were bought by 714 people. One thousand and one fishermen were interviewed about their catches. They caught 3,915 fish totaling 1,107.25 pounds. A computed 176,642 fish weighing 52,375 pounds or 232.74 pounds per surface acre were removed from this lake in 1964. A contour map was completed and the vegetative growth affecting fish populations is outlined in this report. The bottom type was not mapped but it has a thick layer of black muck over most of the bottom. Benthos and plankton studies were not undertaken, Forage production was studied by seine sampling and stomach analysis. Water quality was studied extensively and many data were gathered but no certain answers were obtained. Fish died when exposed to a toxic layer of water which developed in the spring of the year and shifted readily up or down during the summer, Large physical and chemical changes occurred quite rapidly in the upper lake when rains occurred. Detrimental effluent from city storm drains, sewage disposal plant, dump grounds, and from industrial plants in Lubbock entered the lake. Game fish did not reproduce in the lake in 1964, Dissolved gases, hydrogen sulfide and ammonia nitrogen, were always present in copious amounts in the toxic layer when it was present. The pH rose to 9.0 in the fall of the year and dissolved oxygen levels fluctuated widely up and down each day of the year. Numerous fish died from unknown causes. (Believed to be from the stresses applied by the above mentioned factors reducing their resistance to diseases already in the population). Dead fish contained DDT and its metabolites in moderate quantities but not enough to be the cause of death. General cleanup of the watershed to produce better water quality is needed. The thermal stratification should be broken up to prevent formation of the toxic zone. Accelerated control measures should be applied to the sago pondweed, beginning earlier and removing decaying weeds more quickly. A drastic reduction of the bullhead and bluegill population after the water quality and weed problem are overcome would allow the development of excellent game fishing in the lake. --- Page 3 --- JOB COMPLETION REPORT State of Texas Project No. _F-7-R-12 Name: Fisheries Investigations and Surveys of the Waters of Region I-A ' Job No. D-3 Title: Limnological and Game Fish Problems Investigation on Buffalo Springs Lake Period Covered January 1, 1964 - December 31, 1964 Objectives: General: To correlate game fish productivity with physical, chemical and environmental factors present in Buffalo Springs Lake. Specific: 1) To map accurately by contour, vegetation, and bottom type. 2) To determine benthos, plankton and forage production. 3) To determine water quality as related to fishery maintenance. 4) To measure productivity of game fish as demonstrated by survey and fisherman harvest. 5) To determine what levels of dissolved gas, pH, and temperature exist in this lake seasonally. 6) To chart fish location and relative population density in the lake at specific localities at various times of the year. 7) To make bacterial counts on the lake water. Procedures: Mapping The bottom contours of the lake were mapped using a sonic depth determining device where water was deep enough for its use. A transect across the lake was established between known points on a map. By careful ebservation this transect was established on the lake. Timed runs were made with a motor boat on these transects. Depths were recorded at 5- or 10-second intervals depending on boat speed and then plotted on the transect on a map. These soundings produced known depths and like depths were connected with contour.lines. The final copy of the map was produced by an engineering firm in Lubbock. --- Page 4 --- Vegetation Plants of each type were gathered and classified to the extent permitted by personnel and literature available. Most plants are classified to genus unless they are quite common and easily recognized. Attention was only given to submerged plants and aquatic plants which were quite obvious on the water's edge because time to carry the study further was unavailable. A plant hook was used in an attempt to bring plants up from depths where collection by hand was impossible, however, no plants occurred at these depths, Circuits of the lake in a boat were conducted to observe the extent and type of vegetative growth and changes in areas occupied by plant growths Bottom Type Bottom types were not mapped due to lack of-time and equipment. Observations {ndicated a heavy muck over the majority of the lake bottom. Benthos and Plankton Benthos studies were not made this year due to lack of time and equipment. No equipment was ever made available for accurate plankton analysis and this phase of the study is lacking. Neither zooplankton nor phytoplankton were examined. Forage Production Forage production was measured by seine samples and stomach analysis of predacious fish species taken by gill nets. Seining was done with 40-foot one- fourth inch mesh seines and with 20-foot one-eighth inch mesh seines. Water Quality Water quality analysis was conducted in the field and in the laboratory. All water samples were collected with a Kemmerer water sampler according to atandard collecting procedures, Depth of sampling was determined by a 12-inch pulley and a revolution counter. Line was held on a metal storage windlass. Subsurface temperatures were taken by pouring water from the Kemmerer sampler into a Styrofoam bucket and taking the temperature with a thermometer. Dissolved oxygen samples were collected and fixed in the field, using Hach's packaged dry chemicals, and titrations were run in the laboratory. Carbon dioxide and hydrogen sulfide concentrations were determined in the field using the Hach method. ‘Turbidity was measured in the field with a Secche disk and a Jackson turbidimeter was used in the laboratory. Measurements of pH were made with a Hellige comparator in the field and in the laboratory. Facilities for determining Biochemical Oxygen Demand (B.0.D.),dissolved solids, ammonia nitrogen, nitrate, nitrite, and sulfate contents were not available at Slaton. In order to obtain this information, samples were sent to the State Health Department Laboratory in Austin. --- Page 5 --- oe State Chemist Charles Ezell traveled to Buffalo Springs Lake twice and conducted chemical analyses in the field. Water temperatures were determined at 3-foot intervals from the surface to the lake bottom in two locations. These measurements were made once a week beginning July 28, 1964, and are presently being continued. While temperatures were being determined, samples were taken to determine pH and turbidity at the surface, mid, and bottom depths. The depth where hydrogen sulfide occurred was also noted. Measurements of water flow into and out of the lake were made once a week beginning in August. These measurements were made by timing a floating cork, with an x-shaped aluminum vane suspended about 24 inches below the cork, through a culvert of known length and volume at the lake entrance. The vane was approxi- mately 4 by 5 inches in width and depth. Outflow was measured by obtaining average stream width and depth to obtain volume. Rate of flow was obtained by timing a floating twig over a measured distance in several areas to arrive at -an average. Embody's formula was then used to determine flow figures. Productivity Game fish productivity was measured by seining, gill nets, and fisherman harvest by creel census. \ Fish location and relative population density in the lake at various times of the year were derived by comparison of total catch in the different netting zones by nets and by fishermen. Original plans included the use of fish traps to capture fish for marking to avoid the injuries which are sustained in gill nets. Two types of traps were tried and abandoned because they caught too few fish. Study of the fish population was therefore conducted by netting, seining and visual observations. Nine regular netting stations were established and netted once a month during the last week of the month. This report covers data from March through October except for the month of September when the program was interrupted to aid in the rotenone treatment of Lake McClellan. Single units of standard survey gill nets were used at all stations except No. 1 where 2 units of standard survey gill nets were set. The nets were fished submerged along the bottom contours in most areas. Examination of the contour map will reveal the depths of areas where nets were set. Nets 1 and 3 were attached to buoys about 100 feet from shore. All nets were set per- pendicular to the shoreline except number 8 which was set at an angle of approximately 45 degrees to the shorelire pointing downstream. Fish which were in good physical condition when removed from the nets were marked by punching holes in their fins with a one-hole paper punch. Fish taken from net No. 1 were marked by punching one hole in the caudal fin. Fish from net No. 2 were marked by punching one hole in the dorsal fin, and fish from other. nets were marked by punching holes in other fins or combinations of fins. --- Page 6 --- This method of marking was used until tagging equipment became available in August. After the tags were available all largemouth bass (Micropterus salmoides), carp-goldfish hybrid (Cyprinnus carpio crossed with Carassius auratus), crappie (Pomoxis annularis), white bass (Roccus chrysops), black bullheads (Ictalurus melas), and channel catfish (Ictalurus punctatus), which appeared strong enough to survive were weighed and measured before being tagged and released. Sunfish were not tagged unless they were unusually large. Those fish which appeared too weak to survive were kept and autopsied for sex, weight, length, parasites, and stomach contents. Beginning in May, seining with 20-foot and 40-foot seines was done in conjunction with netting surveys in an effort to capture young-of-the-year game fish. Visual observations of areas where nesting of game species might occur were made each time project personnel were at the lake. In addition to incidental observations, circuits of the lake were conducted in a boat with the specific purpose of locating spawning areas and nests. Creel Census Creel censuses were conducted twice a month on a non-scheduled basis. When time was available a census was run. A State vehicle was parked beside the road with a sign approximately 50 feet away from the truck, in the direction from which traffic was coming. The sign read, "Fishermen Please Stop". All fishermen who stopped, whether successful or not, were questioned about the bait they were using, the length of time they had fished, the area of the lake where they fished, and if they were successful, their catch was examined. Examination was done by separating species and weighing and counting individuals of like species. No lengths were taken. At first, voluntary creel census cards were devised and handed out at the entrance gate to all fishermen entering the lake. These forms requested the same basic information as was obtained by the personal interviews. Fishermen were asked to deposit these cards in a box, at automobile window height, as they left the lake. Results were so uncertain that this method of sampling creels was abandoned, Bacterial Study Dr. Kuhnley, a bacteriologist on the staff of Texas Technological College in Lubbock was contacted in an attempt to obtain cooperative aid in this phase of the study. He advised against this phase of the study because techniques for obtaining the wanted information are not entirely reliable. In his opinion the information desired would not produce tseful data and no qualified individual was available to conduct a study. Findings: Vegetation Water Quality Criteria, page 304, Section e, "Fish and other Aquatic life", states: "Algae can be severe pollutants to fish in two respects: (a) they can --- Page 7 --- cause heavy fish mortality through direct poisoning or (b) they can be responsible for oxygen imbalance, thereby killing fish through oxygen depletion or oxygen supersaturation of the waters.'' This phase of possible cause of fish mortality has been ignored and should be investigated because algae growth is at times profuse in the lake. Two vegetation surveys were conducted on Buffalo Springs Lake. One survey was conducted May 28, 1964, after the sago pondweed (Potomogeton pectinatus) first appeared, Sago pondweed is the major plant affecting fish populations 4n the lake. Table 1 is a checklist of plants from Buffalo Springs Lake. Table 1. Checklist of Plants Obtained in Buffalo Springs Lake, May 28 and July 21, 1964. Common Name Sago pondweed Bulrush Sedge Sedge Cattails Eel grass Dock Willow Grasses (undetermined) Weeds (undetermined) Horsetail Potomogeton pectinatus Scirpus validus Scirpus americanus Scirpus sp. Typha latifolia Eleocharis sp. Rumex sp. Salix sp. Gramineae Compositae (majority) Equisetum fluviatile Sago was growing where the water depth was restricted to 5 feet or less. The growth was new and few plants were mature enough to flower in May. Figure 1 illustrates the approximate extent of sago growth in May. Plants found along the shoreline, listed in their order of abundance were terrestrial grasses (Gramineae), weeds (mostly Compositae), rushes (Scirpus americanus, Scirpus validus, and another Scirpus sp.), cattails (Typha latifolia), dock (Rumex sp.), willow (Salix Sp.), and horsetail (Equesetum fluviatile). Only those aquatic plants sufficiently abundant to be easily observed are included. None of the plants listed were profuse except sago pondweed. Much of the shoreline along the upper lake is mowed and plant growth is suppressed. The second survey on July 21 revealed the same species present. Sago pond- weed had spread greatly in most areas and was so dense that an outboard motor could not be operated in it. The extent of the spreading is outlined on the map in Figure 2. Areas covered are approximated from visual observations. No direct measurements were attempted. No further surveys were conducted specifically to determine plant type or abundance. Observations of the extent and nature of plant growth were made incidental to the monthly surveys of the fish population. --- Page 8 --- b= EE. | @ =_ LAKE: OF Fic @ = fTOILETS g@ o a a - { ROADS / DRINKING WATER j / AMUSEMENT PARK | ! BOAT DOCKS AND PIFR> d 23, Pond wee Pe ~——_#i/ Sage nd a | | 4 — | i ee ! Sr i oe i ; Se i > { j : i ee H i ‘ u r é i = ~~ i i H ad Be] \ --- Page 10 --- In August the entire upper end of the lake, from the culvert at the west end of the lake to the first fishing dock on the north shore, became choked with sago pondweed except for a small channel which is outlined as dashed lines on the map in Figure 2. Lubbock County Water Control and Improvement District No. 1 has an aquatic plant mowing machine and in mid-July began mowing the sago pondweed. Mowed plants drifted to the shore and were removed, dried, and burned. Mowing operations began in the lower lake to allow freedom of movement of water skiers and progressed to the upper lake. Areas where mowing suppressed growth of sago pondweed are noted in Figure 3. Mowing allowed easier access by fishermen. The mowed sago was cut at approximately 3 feet below the water surface and remowed as regrowth occurred. These plants provide dense cover for small fish which allows overpopulation by fish species of small average size. The large percentage of bluegills in the fish population is a partial reflection of the dense growth of sago pondweed. The sago pondweed remained abundant in the lake in areas noted in Figure 2 until mid-November when it began regressing. By the middle of December the lake appeared void of submerged plants. This introduces a second manner of affecting the fish population. The dead plants use oxygen for decay, release organic wastes into the lake and provide additional chemical pressures for the fish to withstand. ° The pH readings became quite high, ranging from 8.8 to 9.0 throughout the lake in the fall.. Water Quality It is certain that this annual growth and die off of sago pondweed adds to the water quality problems of the lake. State Health Department records were utilized to determine the average quality of the surface water entering Buffalo Springs Lake during 1963. Table 2 contains the averages of readings as calculated for three different sites. Site l was at 50th Street, site 2 at the entrance to Buffalo Springs Lake, and site 3 was at the Dam. These averages do not indicate the extreme fluctuations which occurred during the year. They do indicate, however, the conditions which must exist in a lake which receives this borderline quality water. Table 2 Average Water Quality at Sites 1, 2 and 3 From State Health Department Records for 1963. Site l Chlorine Ammonia Total H Sulfate Demand B.O.D. Nitrogen Nitrite Nitrate Alkalinit 7.99 356.09 7433 5.88 0.43 0.37 31.24 369.04 Site 2 8.43 417.64 8.38 6.44 1.80 0.22 0.98 322.88 At Dam Site 3 , 8.72 328.00 7.44 3.32 0.59 <0.1 0.36 249.55 During 1963, Leuter's Feed Lots were permitting run-off from their cattle pens to. enter the upper V-8 Ranch lake, an impoundment on the Double Mountain Fork of the Brazos River above Buffalo Springs Lake. The V-8 Ranch lies between Lubbock and Buffalo Springs Lake. This ranch has four lakes impounded on this stream, ranging from an estimated 30-acre lake down to a 5-acre (or less) lake. --- Page 11 --- -9- pePred oe S SURId GNV SNDOd LvoO@ Wevd INS WSISIAY YaLVM ONDINIYG Bae — LEY K \ , se — muna Eg oN AS as EEE “ERGROM GR cA : — --- Page 12 --- -10- Flow in the lakes on the V-8 Ranch is slow and the amount of natural treatmen occurring in these lakes is not known. Bottotn sampling was not conducted, however, deep layers of black muck were observed in these lakes while sampling for water quality. In places the stream flows swiftly between lakes on the V-8. Most of these areas are narrow and shaded by weeds and rushes which reduce the natural treatment afforded. Natural treatment would be improved if the stream bed were wider, shallower, and vegetation were kept down to prevent shading of the water. The lakes act as oxidation ponds and shock load ponds for Buffalo Springs Lake during average flow. When rains occur, however, sediments in these lakes are stirred up and accompany fresh run-off material from the city's storm drains, industrial plants, and garbage dump into Buffalo Springs Lake. Dilution of wastes by rainwater is an alleviating factor; however, Buffalo Springs Lake acts as a catchment and fermentation basin for the great majority of undesirable material from the watershed. This is because its current flow is slow, even during high water settleable solids and many associated materials tend to settle out in its basin. Open File Release No. 51, February 1955, of the United States Department of the Interior, Geological Survey, provided information concerning porosity of soils in the area above Buffalo Springs Lake. Paragraph 2, page 9 states: "The channels of both the Double Mountain Fork and Yellowhouse Creek contain alluvial materials capable of absorbing and trans- mitting considerable quantities of water. Some of the water used for watering lawns, washing streets, and for other purposes is undoubtedly absorbed by this alluvial material in the city of Lubbock and may be the source of part of or all the small flows present in the Double Mountain Fork above the sewage disposal plant. This seepage water, no doubt, is somewhat polluted from various sources and the nitrate content should be greater than that of Lubbock city water but less than that of seepage water in the vicinity of the sewage disposal plant". The author of the release later demonstrated this statement to be accurate. This soil allows seepage from any dirt storage area where polluted water is stored and would allow percolation from fields irrigated with polluted waters in this area. Water quality has improved since the data in Open File Release 51 were being gathered in 1963. The conditions on the watershed still combine to produce a very rich water quality in Buffalo Springs Lake. The lake develops a thermal and chemical stratification, and during the summer of 1964 a layer of toxic substances, including the high levels of ammonia nitrogen (up to 6.5 ppm) and hydrogen sulfide (well over 5 ppm) existed at varying levels below the surface. This stratification existed sporadically from mid-April until September when cool weather caused the thermal layeration to disintegrate. Weekly scheduled determinations of temperature and pH and the depth of the layer of toxic substances were begun July 28, 1964, and are presently being continued. --- Page 13 --- -ll- Sample sites are indicated in Figure 4. Sites had the following depths: W- 7 feet, X - 21 feet, Y - 24 feet, and Z - 52 feet. Site 2 has one deep hole as shown on the contour map, Figure 5. The exact location of the 52-foot deep area at site Z was difficult to sample because of its small size; therefore, sampling was done to a depth of at least 40 feet in the general area. Samples taken across the lake at various locations indicated that the upper surface of the hydrogen sulfide containing layer was almost level. Weekly samples at the four sites were taken at 3-foot intervals from the surface to the bottom and measured for temperature and checked for odor of hydrogen sulfide. Odor was used as an indicator of the depth where the layer began. Surface, mid-depth, and bottom (or lowest depth) water samples were analyzed for pH at the lab. Dissolved oxygen measurements were taken sporadically as unusual conditions occurred at the lake. In July, 114 out of 126 fish caught in net No. 8 were dead (90.48 per cent). Water samples were taken at the surface and at a depth of 8 feet at the site. These samples were extracted at 11:05 asm. on a sunny morning while a breeze was blowing. Water conditions were undoubtedly worse during the early morning hours. Analysis of the water samples from this area showed dissolved oxygen to be 1.8 ppm at the 8-foot depth. The water temperature was 83° F. at the surface and 80° F, at 8 feet. Dissolved oxygen was 9.7 ppm at 4 feet and 10.9 ppm at the surface. Carbon dioxide was not present at either depth and no odor of hydrogen sulfide gas was noticed. A test with chemicals verified its absence. State Health Department analysis of a sample from the 8-foot depth, where the dead fish were located, produced the following figures: pH 8.2, ammonia nitrogen 1.2 ppm, conductivity 2,233 micromhos, nitrite nitrogen <0.1 ppm, nitrate nitrogen 0.5 ppm, phenolphthalein alkalinity 0. methyl orange alkalinity 264, and B.O.D. 7.0. Water Quality Criteria, page 225, under nitrites states: "1, General. In water, nitrites are generally formed by the action of bacteria upon ammonia and organic nitrogen. Owing to the fact that they are quickly oxidized to nitrates, they are seldom present in surface waters in significant concentrations." What rate "quickly oxidized" indicates is not known; however, the sample extracted July 20, was held several hours and mailed to Austin for analysis without refrigeration. It is certain that the 0.5 ppm nitrates are the result of a higher nitrite content at the time of sample extraction. Insufficient on-site chemical analysis has been done. On-site analysis is needed because time and temperatures allow alteration of chemical quality when samples must be shipped to Austin for analysis. : The occurrence of the dead fish in net No. 8 was followed later by live caged fish bio-assays of the toxic layer mentioned earlier. These tests were conducted at site 2 as shown in Figure 3. Fish introduced imto this layer, retained for short periods of time and removed, showed definite signs of distress. Some died within a period of 24 hours. Three tests of the effects of Buffalo Springs Lake water were conducted with live captive fish in live-nets. The nets were approximately 2 feet deep and 1 foot in diameter. They were suspended from floats at chosen depths. --- Page 14 --- ale aes { ee: er eee seme here ! y= a i “Fas, | ame - : #4 “Sing . / a BS x ~ J Ne . / . inn Hh RO me fi 4 < ro! a ie, f a = Bits a 8 TITTY Z-weeksy sam Srate chemi --- Page 15 --- “Aldlife Departaent. Soundines Parks were meda in June ~ July, 196k eueuue and AY SLEVTIM IS 3015.0 berets ae Underwater contours plotted from soundings made by ?. euce the Texas 21 a, ETE ict Zac Ce | 1S a ‘ Improvement District Ho. I tea and Utilities BOFFALO SPRINGS LAKE Water Control and Layout of Building 31! fou i fet RAM Labbeck County --- Page 16 --- -1A- The depth was measured to the bottom of the nets. These nets were allowed to remain submerged within the toxic layer for measuted lengths of time. Test fish were black bullheads of about 5 inches standard length and orangespotted sunfish, (Lepomis humilis) of about 3 inches standard length. Table 3 contains water quality data obtained during the first test on July 8. Table 3 Water Quality at Site 2, July 8, 1964. Depth Temperature _____ Dissolved Oxygen _._ Hydrogen Sulfide Surface 82° F. 9.7 ppm 0.0 ppm 9 feet 78.5° F. 4.3 ppm 0.0 ppm 12 feet 78° F. 0.9 ppm 0.0 ppm 15 feet 77.5" F, 0.0 ppm 2.0 ppm 18 feet 76° F. 0.0 ppm greater than 5.0 ppm Control fish were kept in a minnow bucket at the surface and all were in excellent condition after the tests terminated. In this test, fish were lowered to 9-, 12-, and 15-foot depths. Fish lowered to the 9-foot depth all appeared normal after a total exposure of 3 hours and 37 minutes. These fish were raised to the surface and examined at 10-minute intervals until 3:38 p.m. when varying intervals of longer duration were used. At 6:44 p.m. the tests were terminated. Fish at the 12-foot depth were examined by the same schedule as the 9-foot depth specimens and all but one sunfish were in good condition at 6:41 p.m. when this net was removed. One sunfish had its head and gills entangled in the cloth mesh of the top of the live net, and was dead. Death of this fish was attributed to suffocation as its gills were rendered inoperative by the mesh were it was entangled. The 2-foot height of the live net would allow these fish to rise to -about the 10-foot depth if they desired and they may have done so. Depths to which they were lowered were measured to the bottom of the nets. Fish lowered to the 15-foot depth (2 sunfish and 4 black bullheads) were examined at 10-minute intervals from 3:05 p.m. until 3:58 p.m. when they were left until 4:12 p.m. When these fish were first examined at 3:15 p.m. (after 10 minutes exposure) they all appeared affected. Their reactions were slow and their color had changed. Yellowing of the skin of the bullheads and blanching of the colors of the sunfish occurred. All fish were alive however. After 20 minutes exposure the sunfish in the net were dead, all the bullhead were sick, and color changes were intensified. After 30 minutes, 2 bullheads wexé very sick and the other 2 less lively than before. At 3:47 p.m., after 40 minutes exposure and 3 trips to the surface for examination, all 4 bullheads were quite sick and their fins reddened or suffused with blood at the bases. At 3:58 p.m. 1 bullhead was dead and the other 3 were badly distressed with reddened fins and red flecks on the abdomen (many dead or distressed bullheads examined during the die-offs had these same symptoms ). --- Page 17 --- -1 5- The same conditions were present at 4:12 p.m. At 4:28 p.m. 2 bullheads were dead and the other 2 had lost their equilibrium. At this time all the test fish were removed and replaced with six fresh bullhead specimens and lowered at 4:30 p.m. The fresh specimens were examined at 5:00 p.m. and then again at 6:41 p.m. when this test terminated. When examined at 5:00 p.m. they had all lost their equilibrium and were olive golden in color and their bellies were reddened. When removed at 6:41 p.m. all were dead. The next test was conducted July 17, 1964. At this time the water quality was as is expressed in Table 4. As can be seen, no HjS was present and only 0.5° F. variation in temperature in 17 feet depth was noted. All test fish were left at the 17-foot depth for 30 minutes. None of the fish showed any effects except for a very slight reddening on the stomach and fins, and a very slight lightening in color. No equilibrium loss or any other signs of distress were noted. Table 4. Water Quality at Site 2, July 17, 1964. Depth Temperature pH D.O. HS Ammonia Nitrogen 2 feet 77° F. 8.6 6.0 ppm 0.0 ppm 0.8 ppm 10 feet 77° F. 8.5 4.6 ppm 0.0 ppm 0.4 ppm 17 feet 76.5 ° F, 8.4 3.6 ppm 0.0 ppm <0.2 ppm The last caged fish bio-assay was conducted August 6, 1964. Test fish were 3 orangespotted sunfish and 4 bullheads per live-net. The location at site 2 was changed slightly to allow submerging the live-nets to a depth that insured exposure of all fish at all times to the effects of the toxic layer. Water quality at the site is shown in Table 5. Table 5. Water Quality at Site 2, August 6, 1964, Depth Temperature pH D.0. HS cO. 22 feet 79° F, 8.5 0.0 ppm 4.0 ppm 2.0 ppm Table 6 contains the data from the test. All fish were submerged to 22-foot depth. Each live-net contained 4 bullheads and 3 sunfish. Table 6. Results of Live Caged Fish Bio-Assays of the Toxic Layer of Water in Buffalo Springs Lake on August 6, 1964, Net No. Time Condition When Removed from Layer Condition Next Day 1 5 min. 3 sunfish alive, distressed 3 sunfish alive, color faded 4 bullheads alive, distressed and 1 bullhead alive, red swimming upward flecked and 3 bullheads dead sunfish dead bullheads dead bullheads alive, red flecked 2 10 min. 3 sunfish looked dead, 1 recovered 4 bullheads alive, distressed sunfish dead alive, fine condition bullheads alive 3 15 min. 3 sunfish looked dead, 1 recovered 4 bullheads alive, distressed Frm NNW 4 Control on surface - all fish in fine condition. --- Page 18 --- ih Analysis of the results of these tests indicates that prolonged exposure of fish to conditinneg present in the toxic layer is fatal. It also indicates that shor’ term exposure results in subsequent mortality of the exposed fish. Lack of oxygen would cause distress and possibly would cause the reddening of the fins and tissues; however, there should be no fatalities due to short term oxygen lack alone. 7 E. W. Bonn, in his Job No. E-1, Channel Catfish Study, says: "To observe the effects of low oxygen the dissolved oxygen level was intentionally kept below 1.0 ppm for several hours in an experimental jar. The fry stayed near the top of the water while the oxygen was low, but returned to the bottom of the In another experiment 10 fry were held in Lake Texoma water with less than 1.0 ppm oxygen for 24 hours. All fish were very weak, but all recovered when the oxygen was raised above 3.0 ppm and apparently suffered no immediate ill effects." - jar as soon as the oxygen level was raised. Three of the bullheads were submerged in the toxic layer 5 minutes. They were alive but distressed when removed and died later. effects other than lack of oxygen were killing the fish. exposed 10 minutes was distressed when removed from the layer. have recovered but died within 24 hours. This indicates that One of the sunfish He appeared to The following information was received from State Chemist Charles Ezell concerning ammonia nitrogen content and its effect on fish: "The following are the results of bio-assays conducted here at the lab in San Marcos: Concentration Ammonia Nitrogen #1 #2 #3 Control 10 ppm H9.1 | All dead within 12 hours. All dead within 12 hours. All dead within 12 hours. All alive and okay. 6 ppm H 8.9 All dead within 12 hours All dead within 12 hours. All dead within 12 hours. All alive and okay. 4 ppm H 8.0 All dead within 24 hours. All dead within 24 hours. All dead within 24 hours. All alive and okay. “Water for these bio-assays was from the supply reservoir here on the hatchery. Test animals were also obtained from the "In all of the bio-assays all of the hatchery. test animals exhibited extreme dis- comfort almost immediately upon introduction into the test solution. After a short period in the test solution a redness appeared and deepened until death. Just prior to death the test animals would erratically work the water surface making gasping motions with their mouths." --- Page 19 --- -|/7- There was no ammonia nitrogen analysis of the Buffalo Springs Lake water when the last live caged fish test was made. If synergistic action of HyS, ammonia nitrogen, and dissolved oxygen lack is occurring, future tests should include a more complete water analysis in order to indicate this. Gill netting results indicated that fish enter this toxic layer voluntarily to feed or for other reasons. Fish were repeatedly found dead in the nets on the deeper end within the toxic zone, apparently killed by the conditions existing in the toxic layer. Data from the State chemist's water analysis of the lake on September 22 and 23, 1964, are showm in Table 7. Temperature gradients for sites X and Z are presented in Table 8. This table contains data indicating depth, temperature, dissolved oxygen, and where the toxic layer occurred. Sample stations are shown in Figure 4. Samples were surface only at stations 5, 6 and 7. Surface, mid and bottom water samples were taken at stations 1 through 4. Care was taken to avoid disturbing bottom sediments when water samples at "bottom" were taken. Water in the upper lake, at sites 1 and 2 was lacking in hydrogen sulfide although ammonia nitrogen in deleterious amounts was present. Table 7. Water Quality in Buffalo Springs Lake at 7 Sites and Various Depths as Revealed by Chemical Analysis September 22 and 23, 1964. Ammonia Phenolphthalein Methyl Station Temp. D.O. ele) Alkalinity. pH Nitrogen Alkalinity Orange Alkalinity 1) top 71.5 5.4 1.0 208 8.8 1.93 29 179 5" bot 70.0 4.2 2.5 223 8.8 1.89 40 183 2) top 71.5 5.4 2.0 206 8.7 1.97 38 179 12‘ mid 70.5 3.4 0.5 199 8.7 1.95 27 161 24' bot 70.0 Zak 0.0 195 8.4 1.62 17 178 3) top 73.0 5.8 0.0 213 8.4 1.50 32 T81 12' mid 71.5 4.8 0.0 215 8.4 1.28 31 184 24' bot 71.0 2.2 0.0 206 8.2 1.25 29 178 4) top 73.0 5.6 0.0 220 8.6 1.50 39 181 20' mid 71.0 2.0 0,0 188 8.4 1.36 20 168 40' bot 66.0 0.0 1.5 208 7.8 5.85 0 208 5) top 70.5 5.2 0.5 212 8.9 2.23 33 179 6) top 75.0 4.2 0.0 202 8.4 1.66 14 188 7) top 74.0 4.8 0.0 202 8.2 1.17 20 182 Alkyl Benzene Sulfonate Phenols 2) top 0.078 0.012 4) top 0.133 0.010 5) top 0.072 0.016 6) top 0.104 0.008 7) top 0.104 0.008 --- Page 20 --- -LB- Table 8. Temperature Profiles of Sitex X and Z in Figure 4, These were Conditions on September 23, 1964. SITE X Depth Temperature ___ Dissolved Oxygen 0 71.5 3.4 3 71.5 4.0 6 71.0 3.6 9 70.5 2.0 12 70.5 3.4 15 70.0 1.8 18 70.0 2.0 21 69.9 1.8 24 70,0 2.2 SITE Z 0 73.0 3 73.0 6 72.5 9 72.0 12 71.5 15 71.5 18 71.0 21 71.0 24 71.0 27 71.0 30 71.0 33 71.0 36 71.0 - Hydrogen Sulfide appeared, strong odor 39 67.0 40 66.0 Hydrogen sulfide appeared (strong odor) at the 36-foot depth at site 4 in the lower lake. At all sites ammonia nitrogen was present in amounts over 1.17 ppm, and at the 40-foot depth at site 4 ammonia nitrogen was present at 5.85 ppm. The layer of toxic substances shifted readily and usually accompanied a a° (or more) break in temperature. It occurred at pH ranges from 7.8 to 9.0 and temperatures from 62° F. to 80° F. Figure 6 contains data encompassing the ranges of readings of pH, temperature, and depths at which the toxic layer occurred at site Z. Hydrogen sulfide is toxic to fish in proportion to the amount of unionized hydrogen sulfide inthe water. Water Quality Criteria, page 200, paragraph 2, states: "The sources of hydrogen sulfide in water include natural processes of decomposition, sewage, and industrial wastes such as those from tanneries, paper mills, textile mills, chemical plants, and gas-manufacturing works." Few industrial plants on the Buffalo Springs Lake watershed and the H25 present is formed by anaerobic bacterial action on natural or introduced organic wastes in the lake. --- Page 21 --- ! tbe es “7 _} ad “nel = _ CITPeT pI yyy try rere HE q pehireray atnauaesancces: t ~ | eet hlel telistneleoleetehe Later 4 fej petal aie ct aesceces eal yceeeseesdagguecanepeges! aecaaenae od ty Bes ion RPEp hy port oh. enna naan ise tft | caneeeee Peer) Seuseeee Bantry meseenaauaaunageneedgs COT! Pat Phe SOCCE CCE yt) Eee Saeeen Saeeseeneees “ET. Co cc beErEL EE CPEEDE H s cers ert tt tented bt pop. | wht Ep pb ed : Ht eed herp ft +o Pept am an Pete oa Ceres ee Por Ceeee eee saeenan iaseneeee~s a one “ ‘ Coo hon cer aan es eee a Ob Cec anon eee PTT TT a COC - Saeennen Sacer CCCs ia eeeeeen “Tarren Coe Case CO nanan Pos CeCCOA Senne cS PELE PEEEEEE Pra CR sesgSue) Seeseeeeaeees an ete BOGEECGEL SEU CESSSBaEE EEC Beaune s MEH 7 a GEER EEE EEE Se CCCs cco S000 0SS SSSR See one b Hao CeCe ae Cocos co 7 COCOA Sch AT HERE EH ECE EEEEEEEEEEEEEECEEEEEEEEE CRS BE CCC Ss ce anae CCC BRE CE ERE Cee CAs Ce Th Hes Sth REECE COCO eer Seen oH . acnee Ce Cooceceee SeeennEe a: CEE a A oN CO oer \ASRCSRSSRSRSSE RR Co SeeeSe80L280 Suh SeneSeenn8 Perr SSRRSS RSS SESE eee Sceeeeunan COCO RECO HCCC ac) SaenneS HHH a om one SSeeneeeene EEEEEECEEPY Coo Po anneee PH auasesen Coe ee on BREE eee LECCE rss seam BEC EECEEECe rer re eC iccccaece COCO CREST PEE 5 Coo cekR en ene CC ete aang BEECEEEEE EEE ay es eee . EEC EEE CECE EEC EEE CE GEE er CCCP R Er CCCs PERE EEE EEE EEE EH EOP GAS ec Ch REEEEEE CEE ERO tal PERE CCC are Cee a OO EEE EEC EE EEE EEE EEE EEE a $9 RCCCCCCCCeeeeeeeree ere CeCEEC EC CECE eee cece et STESEEDePESeeeeeneee Cocco RN SRE A ee ee es } JSS 0000000 eee eS Coen Pree FA Scere CCCP sa a ee eee SeRRe RRO Se PEER EEEEEEEEE EEE EEE EERE REECE PET oe PEE ane SSS SGS000 4808 COC eee SSRRSKONE rH EEEA CCC eee nc COE ECC CCC CCC eee et BRRCEECEEE EEE LEH SOSSSeee508 ECCCE CCRC CECE Co EEEEEEE Eee cor CoCr COPS Err eee EEE HEE BEER EEE EERE EERE EEE So SESECEEEEESSERSAZGGAESEEETEEEEEERERESEEEEEEEEECE PEERS oo EEEEEH PEE Pee COO oC aeenne a Ne Ho cA cl Titer SS CEC CCC ann6 saan COCO CCC Cocco Co Bee SEE EEE CEE Nea BEPC an le SESREeeaEe Coco i am hn RACE aan SGneeeaenes CCPC eccer ry EEE SUSGe0CX J0RS6RSReen COCO CCC eee FEEEEEEEEEEEEEEEEECEEEEECEEEE TEER RE EEEEEEEEEEEPEEEEEEEEEEEEEEEEEEH PEPE err CEE CE ee PERCEEEHH COCCeECCCeE CCC Sanneeee CCCCCCCceeecy PAE ee co EERE CCC : SHEE COCO HEEEEEE Er SOS SSSneE8 SaSeeeenene8 serereerct EEE BeEEE EE PEEEEEEEH BEE EEE EEE EEE Cc] = --- Page 22 --- -20- The 417.6 ppm average sulfates in the surface water supply (Table 2) provide abundant food for plants, algae, and plankton. This tends to produce corollary pollution by creating a dense algae layer in the upper 2 feet of water. The organic wastes from these growths is another source of materials for bacteria to act upon in producing HS. Ammonia nitrogen is soluble in water to 100,000 milligrams per liter at 20° C. Hydrogen sulfide is soluble to 4,000 milligrams per liter at 20° Cc. and one atmosphere of pressure. At depths of 20 feet and below, pressures are greater and what solubilities, chemical reactions, or varied metabolic effects occur there are not known. Water Quality Criteria, page 133, section e, states: "According to many references, the toxicity of ammonia and ammonium salts to aquatic animals is directly related to the amount of undissociated ammonium hydroxide in the solution, which in turn is a function of pH as explained under "General" above. Thus, a high concentration of ammonium ions in water at a low pH may not be toxic, but if the pH is raised toxicity will probably increase. Ellis found that the toxicity of a given concentration of ammonium compounds toward fish increased by 200 per cent or more between pH 7.4 and 8.0." Also, two paragraphs later, "The toxicity of ammonia to fish is increased markedly at low tensions of dissolved oxygen." The behavior and strange death pattern of the fish used in the live caged fish test suggest that synergistic action may be occurring between ammonia nitrogen, hydrogen sulfide, and dissolved oxygen inthe toxic zone, Those fish which were submerged the longest period of time survived best. Those fish which were exposed longest became unconscious while in the toxic zone and could not actively attempt escape when removed from the layer. The fish which were still capable of coordinated action swam vigorously upward accelerating their metabolic rates. Fish which actively attempted escape hada high mortality rate. Ammonia can originate as a direct pollutant but this is not the case at Buffalo Springs Lake. Water Quality Criteria, page 132, under "Ammonia" states: "in surface or ground waters, however, it generally results from the decomposition of nitrogenous organic matter, being one of the constituents of the complex nitrogen cycle.", and one sentence later, "Rivers known to be unpolluted have very low ammonia concentrations, generally less than 0.2 mg/L as N." N in this case is the total ammonia nitrogen content as NH3, NH,OH, and NHyt. The test for ammonia as N is the test represented in tables and graphs in this report as ammonia nitrogen. It can readily be seen from field analysis by the State chemist that ammonia nitrogen is considerably in excess of 0.2 milligrams per liter in Buffalo Springs Lake. One milligram per liter translates roughly into one part per million (ppm). Flow data were taken each week beginning in August anticipating the feasibility of draining the toxic layer from the bottom of the lake if flow proved to be sufficient to prevent buildup of the layer. It is doubtful that this will be possible because inflow averaged only 7.52 cubic feet per second from August 9, 1964, through November 25, 1964, This average is probably high because several readings were made which were inaccurate and had to be discarded, Light rain occurred on November 16, 17 and 18, increasing the reading for November 18 to --- Page 23 --- =91« 26.46 cubic feet per second which would tend to increase the average considerably for the short term data presently available. These measurements are being con- tinued, and possibly a period of trial drainage from the bottom layer of the lake will be conducted in the spring of 1965 as the layer is forming. Examination of weather data, obtained from the U. S. Weather Bureau, in- dicated that surface water temperatures correlated to the average daily temperatures with a few hours lag in attaining those temperatures. In several instances the water temperature lowered when the average daily temperatures did not. Rainfall, in one instance, caused shifting of the thermal gradient in the lake when daily temperatures were fairly stable. The temperature gradient of the lake water on July 28 was quite steep as illustrated in Figure 7. The odor of HyS gas appeared at the 18-foot depth at a temperature of 78° F. close to the upper end of the thermocline. The epilimnion occurred from 15 feet to the surface. The thermocline existed from 15 feet to 36 feet and the hypolimnion occurred from 36 feet to the bottom. The epilimnion is a zone where temperature changes are less than 0.548° F. for each foot change in depth. A thermocline is a zone where temperature changes are in excess of 0.5489 F. per foot in depth, and hypolimnion temperature re- quirements are the same as for the epilimnion. In all figures showing temperature gradients, anaerobic conditions existed in the area below the upper limit of the toxic zone. Fish could not live in that area. On August 4 (Figure 8) the epilimnion extended to 15 feet and the H)S layer began at 15 feet. The thermocline extended on down to 33 feet and from 33 feet to the bottom was hypolimnion. On August 12 (Figure 9) and August 19 (Figure 10) conditions remained fairly stable. On August 27 (Figure 11) the epilimnion was 21 feet deep, the H)S layer began at 21 feet and the thermocline continued down to the bottom. It contained an unusual temperature inversion. Reference to weather data did not explain the inversion. in terms of daily temperatures. At times during sampling the most intense concentration of HyS was at the upper limit of the toxic zone. No tests were run to determine if a temperature inversion existed at these times. On September 2 (Figure 12) the sudden shift of 79 in 3 feet seen on August 27 had smoothed out and general epilimnion temperatures had lowered from about 79° F. to 749 F. The HS layer began at 27 feet. The thermocline began at 30 feet and went down to the bottom. The inversion layer remained at 42 feet although it was less abrupt with only a 3 degree rise back to 68° F. at 45 feet. On September 9 (Figure 13) and September 18 (Figure 14) there was little thange in conditions except the loss of the inversion layer and general cooling of the lake water on September 18, following several days of low average daily temperatures. On October 6 (Figure 15) additional cooling is evident; however, the H)S layer still appeared at 33 feet at 62° F. The toxic zone disappeared when the --- Page 24 --- Saeneeean Preset co qCGGSCGSene COP REE Ee aacSer un Ppp Tt a Cs He rte icv Am bled ht 4 Pere Fe SSRSSSSRREE im eee ae |_| SRG), VES CRRA -20P ABR a” | tert hol OT tt | AW 7300 4- Cees e SSeS Sacae Sanaa a SaaaaaaaEEaaESSeSaeSSeee ee Beueseare ces a ae = Perry ae eC cor HH anau CCC fem ier ATT EEE EH FEE EEE TH CCC FEECPiaiS App Sars] EEC Cee L Lune SH vam SC tthe pita es = 2A eee HHH ee SRE ee EEE EHH SSR Pe ee ee BUGENE DICTZGEN CO. --- Page 25 --- POC mane rity im ; ies TRITITYy aan EERE EE EEEEEFE-EEEH Atay at ee | nae ah naaee Coco ; SCC HH 7 i an TEEELEL | eaeae “FH = COCO 4 tt Lf. I ‘eas OCCT ea Dr eae sein, TEE (Rees Reese OCC ET Leet. an “AEE ae CECE i ani TC Seeeenee SSRS RRS Ree, aa TTTPTT Pry | ght PP) el ! eee oF CCT Tee + : ~ Ce ae SER geaEN Bae COCO ] ~ S00 S es ee aa C on oaeeeeSSeEee SSaSeeeee : c a S0RS 000008 00S SSR Rees eee ian é CC SSSR ReeeeRe8 Ce COCCI CECE Ce eee Peer ian | EEE EEE H+ Coo mame | COCO CL meee Ag Cc cs rearene | as CI BOE ere rbtat CCr CeCce i nen COCO COC CCCcce HCCC e See0nnn CCC CCC runes TOF HCC CCC aee0een acne CoCC eee Cer CCC Paseeen A aaeeeeeae CCeeeey Cooler Ay CLC Saneeen van Hi Wwe Ss PCE erie ee rligem ttt ttt ritttiiitttit ttt sesuunsunssvsccesdvccedncee avave aaa PHAGE H COCO CCOCCCCeCeeeee pee 4 a SeeenEE Hh aan COCeceoreeee CCC Sans EERE ECC Corry roe COICO co COCCeeeeeeey H EEEEEEEEEEET EEE a i re eam LF auliremne h PEPE Pere reer re] EEEEECE EEE EEEEEE ELEC EERE ee REE sees Perch cricec ee Pe COC PEC CCC EEC Eee CCE eee eecce eeer ) ¥ 8 OO 0 EEEEE COCC CeCe PEE SERRREGSS ESR COOL COC er SeSe0RSe0058 COC CeCe eee . PEER eH Cor SORCoan emo CECE CCC CCC ECC eee eee eee CCC SECS EEE COC CC POCO CECE CECE EEE EEE EEE rere CCC eee PEEP CCOCCC ECC aan SRSSSSS0S See CECE CCE COC ECC eee BEE COCO PEE EEEEECCECE TSRREGUEE Sey sergneseeunnees0000uueeeeeuueeeeeee¢seneeeee0eeeeesceseesesseeses ¢ core BREE EEE EE eee HH Sc COC CEE EEE rH SOnn)) Shen eee SSS Co Cee cr eee COCO ECC Se _ SSRh ROS ee eee BEER Cc COCO COCO Eee eee COCeCCC Eee Saeeeee8 Senne nee COC CCCCCeeec cece COCO ECC CCC ECE FEEEECee S00 DS SSeS eee Ve COCO ECE ECC eee eee CECE EEEH Po Se ee BLOC CCC eee CoOCeece eee PCREECCCEEEE EEC TOSEEE EERE aann SSSR0C SCSsS ESSE CoCr POE Cee PEE EEE =a co Coe 4 CECE Ee HEH Cc PEE He SA OCC C EEE Eee eee eres 4000000 S0 SSeS See SEESEEEEHEeS Tec [pseu )UauuGaneeeUnnnceeeneesueeeedseeeeesseenseeeenceess=eeeesce CACC rr ge rie A sporestatatcarie af dy Susstesbeeetenees pen uaneens Seacesneuseaeeeeacs Seeeee00058 EEEECEEEEEEE EERE EEEEEEEEEEEEEEEEEE EE EEEEEEEEEEEE EEE EEE CECE 66 REE EE EHH Seaman COC CCC EC CCC ECE CEE Cee EEE Pere cco COCCI EEC EC Ee eee r CCHS Coo a SuSueur 2-GeUS000 57 SS6S6R0 7) SenSRGER. SALLLICT yA BEET rar Senne _ Ee Coc Poe Fe Pierre a errr PERCE eee Sennen PEEEECEE EE SERSRSRERne Benen Su uuasaeeusesssecessseesseers7eeserenneeeeeneTaeeeteTreeeeeeETeTeeeeeeeeeeeeeer® S00 RRS R COCCCCC CeCe cc Ban DAE SAB eT: “SPC meee EECCEEEEE EEE EEE EE EET EEE EEE EEE EEE EEE EEE EEE 6244/8 2 a0, 2-7 ee ee 0 8 ON A Oe OO Oe SO OH OO OO OP RUGEME OIETZGEN CO. --- Page 26 --- a auee TTT lb Sei titit HHH a a ane Eee aan ee SRR Prey rT AAS aa 108 | PTT TTT Aa SSBeEREE MI OHHH ys ore Sa Le 4 Lp LTA zen PT tA TTT Coe ee! rave ma) Geaceaanen Saekee ae PE Var earney || ae AAS Aes ad | Lette tt bb is Sy = Py PEC Lt PAC ma Me 2.4-4)- 0/7 a AEX ly SREY SRE RRR ~Rix HH Beene ae FECCH RCE eet eth SEE REE RE necan (ay JSeBEESESEESREESE ae Peer re Pi am Pe rd aan Rie 6g Tol Ae CCCP Tt eA AGW oie Ae pt Pier GEER EEC Ee EEE TAREE Perey re 2osseeeenenee seen Et pe Pit ccc PALI YI arr mm 7) Cc PEC COCECCeC eC Cee aann PEEEEECEEEEE i 7 rt re an aay ; ri ane xf sua aan ie EE FEE rH Sol | aa Si | = ee RUGELVC OS TVGEN CO. Pir ety meeevasertberaeee PPP aneeeee EEE EEE aa enone COCO ee Seon mi ~~ aan Ceres a AK [| Peery et Pry --- Page 27 ---…