A LIMNOLOGICAL INVESTIGATION OF JORDAN LAKE, MICHIGAN WITH 9ARTICULAR REFERENCE TO THE ALGAE WHICH CAUSE. "WATER BLOOM“ Thesis for Hie- Uegree of M. S.» MICHIGAN STATE COLLEGE Wilbert Ernest Wade 1948 THESIS This is to certify that the thesis entitled A Mmological Investigtion of Jordan lake. Michigan with Particular Reference to the Alge which Cause "Water Bloom." presented by hire Wilbert E. Wade has been accepted towards fulfillment of the requirements for __.Mn__s.n__.degree mm 0 ”Qmw Major professor m o .- -Onr*-— a. __ _‘___-___ __ _ - A LIMNOLOGICAL INVESTIGATION OF JORDAN LAKE, KICHIGAN WITH PARTICULAR REFERENCE TO THE ALGAE WHICH CAUSE "WATER BLOOM" BY Wilbert Ernest Wade pl- A THESIS Submitted to the School of Graduate Studies of Michigan State College of Agriculture and Applied Science in partial fulfillment of the requirements for the degree of MASTER OF SCIENCE Department of Botany and Plant Pathology 19% 3&3113’95; TABLE OF CONTENTS I. INTRODUCTION Page A. History of the Investigation . . . . . . . . . l B. Scope of Study . . . . . . . . . . . . . . . . 3 C. Acknowledgements . O O O O O O 0 O 0 O O O 0 lg II. DESCRIPTION OF JORDAN AND TUPPER LAKES A. ‘Location , . . . . . . . . . . . . . . . . . . 5 B. Geological History , , . . . . . . . . . . . . C. General Physical Characteristics . . . . . . . 7 D. General Chemical Characteristics . . . . . . . 10 E. Phyt0p1ankton . . . . . . . . . . . . . . . . . is F. Other Algal Growths . . . . . . . . . . . . . . 13 G. Higher Aquatic Plants . . . . . . . . . . . . . 13 H. Fish and Fish Food Organisms . . . . . . . . . 15 III. "WATER BLOOHS" AND RELATED FACTORS A. History of "Blooms" and Related Literature . . 18 B. Organisms That May Cause "Water Bloom" . . . . 22 C. Injurious Effects of "water Bloom" . . . . . . 9h D. Chemical and Physical Factors Affecting "Water. Blooms" . . . . . . . . . . . . . . . . . . . .30 IV. DATA AND MEASUREMENTS A. Methods and Procedures . . . . . . . . . . . . A3 B. Data 0 O O O O O I O O O O O O O O O O O O O O 52 v. DISCUSS 101‘! OF RESULTS 0 o o o o o o o o o o o o o o o o . b VI. TREATHENT AND CONTROL . Page A. Types of Treatment Other Than Copper Sulphate. 102 B. COpper Sulphate, Use and Objections To Use . . . 10h C. Treatment of Jordan Lake . . . . . . . . . . . . 113 D. Brighton Lake and Copper Sulphate Treatment. . . 11% VII 0 CONCLUSIOIIS O o o o o o o o o o o o o o o o o o o o O 0 118 VIII. SYSTEHATIC LIST OF ALGAE IN JORDAN LAKE INCLUDING PLATE AND PLATE DESCRIPTIONS . . . . . . . . . . 122 Ix. BIBLIOGRAPHY . . . . . . . . . . . . . . . . . . . . . 166 A Limnological Investigation of Jordan Lake, Michigan With Particular Reference to the Algae Which Cause IWater bloom". I. INTRODUCTION A. History of the Investigation In many'Michigan lakes a dense blue-green algal scum, which develops at the surface during summer and early fall, often becomes obnoxious to vacationers, swimmers and others using the lakes for recreational purposes. Operators of municipal water-works may also experience difficulties because of odors and tastes imparted to the water by these algae. Control measures for such superabundant growths, often called 'water blooms", have been studied in many states, but available literature fails to show that investigations of this nuisance condition and remedies have been reported in Michigan. Although not all of the 5,000 lakes in Michigan are subjected to this obnoxious condition, many in southern Michigan are, especially those near centers of greatest population. Thus a determination of the causes of such con- ditions and development of methods for their correction obvi- ously would be of great benefit to the people of Michigan who seek to enjoy the recreational facilities of lakes. Secondly, correction of algal nuisances would help maintain the excel- lent reputation of Michigan lakes among out-of—state tourists; thus benefiting Michigan citizens who earn their liveli- hood by operating beach cottage resorts, boat liveries, bait and sporting goods stores and other recreational enterprises related at least indirectly to lakes. The occurrence of a "water bloom" condition at Jordan Lake, Lake Odessa, Michigan, first came to the attention of the writer in May, 19h7. A group of local lake-front property owners had previously petitioned (Oc- tober, 1946) the Michigan State Department oleealth for a survey of Jordan Lake. This survey was to determine whether pollution was occurring in Jordan Lake from the municipal sewage plant effluent and if so, whether the pollution was a causative factor in the "water bloom" condition. Accordingly Mr. R. G. Poster of the State Stream Control Commission conducted a survey in October, 19h6, but detected no pollution from sewage. Mr. Foster suggested to the residents interested in the "water bloom" condition that they confer with Dr. G. W. Prescott, phycologist at Michigan State College, who was familiar with algae problems associated with water supplies. A group of residents, after having organized the Lake Odessa Improvement Association requested Dr. Prescott to make an inspection. Dr. Prescott, Mr. Foster and the writer visited Jordan Lake on May 12, 19u7, made some preliminary water collections, and interviewed the officers of the Improvement Association concerning the possibility of the writer conducting a survey of the lake. Subsequently, I. arrangements were made for the writer to undertake a study of the biological and limnological conditions of Jordan Lake under the direction of Dr. Prescott. The Improvement Association gladly offered their assistance, including the use of a boat and motor, and a small fund to defray trans- portation costs. The State Stream Control Commission continued their investigation of Jordan Lake and officially condemned it becauSe of pollution on July 12, l9h7. Their investigation indicated the presence of sewage pollution on and around the municipal beach and determined that the location of the pollution changed according to wind direction, thus creating a continuous threat from pathogenic organisms at the municipal beach and all areas in.the northeast one- third of Jerdan Lake. (See map). The report also recom- mended that additions and improvements for the village sewage treatment facilities were necessary to protect the natural waters of Jordan Lake against repeated contami- nation from untreated sewage. The Improvement Association realized that additions to the sewage facilities would not necessarily solve the "water bloom" problems, and so were willing to support the writer's survey which had begun June Euth. B. Scope of Study The primary purposes of the survey were: 1. To determine what organisms were responsible for the f. profuse algal growth and to learn at what time and in what quantity, objectionable organisms occurred in Jordan Lake. This would include also an examination to learn why these organisms formed obnoxious scums. 2. To determine whether there existed a correlation between limnological factors, such as water chemistry, and the ”bloom" conditions. 3. To determine by chemical analyses, the sources and quantities of fertilizing substances entering the lake, and the relative fertilizing capacity of the lake itself. h. To determine effectiveness of methods of algae control by the use of capper sulphate. 5. To record, if possible, a year-around analysis of lake conditions (chemical, physical and biological) so as to determine where the I'bloom"-—producing organisms wintered over and to learn at what time chemical treatment might be administered to be most effective. C. Acknowledgements The writer wishes to thank Dr. G. W. Prescott for his assistance in many ways during the time this study has been in progress. His considerable knowledge, generous advice and helpful criticism have been of great value. Acknowledgements are also due Drs. G. S. Steinbauer and F. L. Wynd and Mr. Herman S. Silva of the Botany Department of Michigan State College for their'helpful suggestions. I wish to thank Mr. F. E. Eldridge, recently of the Sani- tary Engineering Department of Michigan State College for (A the use of the Sanitary Engineering laboratory facilities and for his generous assistance in chemical analysis pro- cedure. Also, I wish to thank Drs. E. N. Transeau and C. E. Taft of Ohio State University and Dr. F. Drouet of the Chicago Museum of Natural History for reviewing some of my Ideterminations and for the identifications of a number of Species. Acknowledgements are also due the Lake Odessa Improvement Association, especially to Messrs. Emmett Blakeslee and Ernest Bertotti for their cooperation during the survey. II. DESCRIPTION OF JORDAN AND TUPPER LAKES A. Location Jordan Lake borders the village of Lake Odessa, and lies in Wbodland Township, Barry County (T h N., R. 7 W., Sec. 3, 4 and 5) and Odessa Township, Ionia County (Sec. 33 and 3A). Tupper Lake is situated in Odessa Township, Ionia County (Sec. 26, 27, 3M, 35) and lies approximately one mile northeast of Jordan Lake, being connected to it by a shallow partly artificial channel. B. Geological History Jordan and Tupper Lakes are glacial lakes, having I - been formed contemporarflslwith the Arkona Lake stage of the Pleistocene Period. The Lansing moraine was laid down I-l L- ‘ w ‘7‘-.— . . ‘ - I. I .‘ o. “f '. . . . . I " . ‘ 'j . . o o g. '0‘ . . ' ' o e o - . t n O. .0 ¢ ‘. . * ' ' ‘ O o e \ o o q I * ' ‘fl .. '. .‘ .' " " " '0’. 0 p '. ‘ D . I. \ a . 2m Io emos SKLWO’VSI do: ;‘Lc839 is'rsna I: In ., \ Io Tedmun 3 To enoéssejiitneht and TC? The sun" :1 '-r ‘ J sesehO sic: an: art osIT ace atnsnewheixon£" .P ’3: “ ‘ tvsmmfi .eTesoM o: {Iisioenss .nnidntncnss f . " 1 I .3311”5 ”0:3”?99(C0 viedfi Tot idicdvef 389f”l fi' -f 0 ‘ I 3525s EETTUT Tvzn Ti::cL To TCITTIEDBES .' uciinncd .A I has .nassso 9134 To ensiiiv as: gass~ou efisd v- ..w y .s ..E J T ttnncO-Tnm .qzaenwow bani ~. ‘ =::? .99?) rdanod‘aznof .qldenwci ssaebo has (a-baz f .r «.s .ntdenon 363360 fif‘j’tnfiffa sf eMsJ women? viewsmixndqes eefI Ens (d? :3? eYS .69 .99?) :v v.~ ~'- I it 03 Dawns-{moL 3nled .einJ nei.ca'In issenw":~ a'7r ep- .Eeunano Isfoifbt a {Ififinq w';.-.. . .- Wf+3£7 r"3$}:°£09§5 .8 SHIVCS .eeasf Interim ems seinfl’weqqu has --‘~-' 911:! To ensue $711M sucrfvz}. 38:. flintakmgwwjm awcr etsl :ET'QElsenw sfijansd'edT .roITeS r :w:= ’ I" 86 LANSING HORAINE fiHO 0-9 555 Ag (G. 2&3 o°°Q 02 _J 08 “”8 05 In L‘ t n I 5.! g E .9: 3’ U 3 E23 LANSING DRAINAGE a PRESENT MARSH LAND cf 0 ;‘. E 3SE ( A“ 4m A) .45 9-1 DJ 1... u. D< ll' If’ -r In along the southern base of the present Jordan Lake (see geological map) during a halt in the retreat of the Saginaw lobe of glacial ice. Drainage water from the glacier ice to the northeast flowed in a southwesterly direction through.the Lansing Channel cutting the moraine. As the demands upon this area, a valley train, lessened, the water followed roughly the general area now occupied by Thorn- apple River, the outlet to Jordan.Lake and Tupper Creek, the inlet to Tupper Lake. The area of the present Tupper Lake also lay in the valley train mentioned above. This lake has remained a body of water in the original drainage- way, as has Jordan Lake, because of the greater depth of its basin. C. General Physical Characteristics Although Jordan Lake is well-known in southern Mich- igan for its fine fishing, no attention has been given to fits limnological nor biological features. Jordan Lake occupies approximately an area of 1,000 acres. The long axis, 1% miles long)runs in a general northeast~southwest direction. The width varies from 5/16 of a mile at the northeast end to 1 1/16 of a mile at the southwestern end. The shoreline circumference is approximately 4 miles. The lake margin is shallow and has a gentle slope completely around the lake as evidenced by growth of both emergent and submerged vegetation. The average depth is estimated at 20 to 25 feet, the northeast end being 0-25 ft. deep and one depression in the southwestern end reaching a depth of 75-80 ft. according to local sources of information. Life-long residents of the village claim that a current of spring-fed water enters the lake at the northeastern end and maintains a distinct channel through the lake. This last information has not been verified by the writer. The Thornapple River is the outlet of Jerdan Lake arising at the southern end. The lake is fed at the northeastern end principally by the channel from Tupper Lake. This channel is shallow, supports heavy growths of submerged and emergent vegetation, and during the summer becomes almost stagnant. This condition exists during dry seasons when the Tupper Lake water level becomes low. Inasmuch as both Jordan and Tupper Lakes have a level of 812 feet above sea level, the flow in the channel between them is not great except during rainy seasons. The storm sewer effluent from the village flows in an- open ditch, from a point approximately 100 yards from the highway (map symbol as), then parallel along the highway for 250 yards to the point (symbol see) where it enters the lake by a culvert. The municipal sewage plant effluent enters the center of the northeast arm of the lake by an underground pipe (symbol med). This plant is composed of 6 septic tanks, each of 15,300 gallons capacity. 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Chemical Analysis of Water and Sewage 69 Chemical Analysis of water and Sewage (in parts per million) Station - Inlet Methyl Orange Alk OH 003 H003 N02 N03 TOT N July 19,u7 0 0 183 .001 .06 1.8u8 Feb. 28,u8 0 0 170 .01 .3. 5.1u Mar. 28,u8 - — —-- ---- -— ---- Apr. 16,u8 0 0 150 ,.02u .12 3.0a May 2,48 0 0 169 .028 .5 ---- May 16,h8 0 0 150 .028 .8 3.2 May 31,h8 0 0 17h .01u .1u 3.2 June 1h,h8 0 0 172 .007 .lh 2.88 June 27,u8 0 0 182 .007 .06 2.88 Ju1y 8ju8 0 0 171 .002 .08 3.0a July 22,h8 0 0 171 tr .oh 2.8 Aug. 5,h8 0 0 182 .002 .06 2.78 Aug. 21,h8 0 0 178 tr .1 2.56 II .\ July 19,n7 Feb. 28,h8 Mar. 28,h8 Apr. 16,h8 May 2,h8 May 16,h8 may 31,48 June 1h,M8 June 27,48 July 8,fl8 July 22 ,18-8 Aug. 5,h6 Aug. 21,h8 71 Chemical Analysis of Water and Sewage (in parts per million) Station — Storm Sewer Methyl Orange Alk OH 003 H003 N02 N03 TOT N 0 0 322 .031 .03 1.u 0 0 159 .08 .07 5.uu 0 0 220 .168 .3 6.08 0 0 2&9 .2u0 .1 13.6 0 0 3&3 .2 .8 12.8 0 0 245 .15 2.4 12.8 0 0 -3u8 .15 .12 1n.u 0 0 357 .1 .26 13.6 0 0 365 .028 .017 12.h 0 0 330 .088 .06 14.u 0 0 132 .088 .12 7.6 0 0 396 .0u5 .08 9.28 0 0 393 .01 .03 11.0 A (y Chemical Analysis of Water and Sewage (in parts per million) Station - Sewer Effluent Methyl Orange Alk. OH 003 H003 N02 N03 T0T N July 19,47 0 0 450 .034 .04 17.6 Feb. 28,48 0 0 371 .5 .7 24.8 Mar. 28,48 0 0 318 .5 .8 24. Apr. 16,48 0 0 314 .24 .4 25.6 May 2,48 0 0 386 .17 .28 28.8 May 6,48 0 0 . 334 .12 3.2 15.2 May 31,48 0 0 382 .04 .1 25.6 June 14,48 0 O 392 .034 .1 27.2 June 27,48 0 0 397 .034 .017 30.4 July 8,48 0 0 285 .014 .2 - 28.8 July 22,48 0 0 242 .02 .4 9.6 Aug. 5,48 0 0 348 .02 .06 28.0 Aug. 21,48 0 0 354 .01 .03 32.0 July Feb. Mar. Apr. Chemical Analysis of Water and Methyl Orange Alk. 19 .47 28,48 28,48 16,48 May 2,48 May 16,48 May 31,48 June June July July Aug. Aug. 14,48 27,48 8,48 22,48 5,48 , 21 ,48 OH O O O O O O O O O O O O O CO} 20 0 0 0 22 0 42 56 58 60 64 26 46 H00 116 60 123 155 139 153 153 88 82 35 65 11 88 3 (in parts per million) Station — Lake NO .002 .014 .014 .034 .028 .028 .044 .007 .001 .014 tr .001 tr Sewage NO .04 .04 .02 .08 TOT N 4.8 6.4 5.76 3.08 3.36 2.96 3.84 2.88 2.96 3.28 3.84 3.4 2.72 II Chemical Analysis of Water and Sewage (in parts per million) Inorganic Phosphorous Inlet Storm Sewer Sewage Effluent Aug. 5,48 .014 .028 .06 Aug. 21,48 .024 .032 .032 Lake .015 .0084 3. Other Determinations and Measurements 75 76 DISSOLVED OXYGEN—-—pH---TEKPERATURE READING DATE 0.0- TEMPERATURE pH p.p.m. Degrees Centggrade 19“? Staig Sta.l Sta.2 Sta.3 Sta.4 Sta.l~Sta.2 Sta.31Sta.4 June 24 11.2 20 20 20 20 8.5 8.6 8.5 6.4 July 1 10.0 22 22 22 21 8.5 --- ---- 6.7 July 9 7.6 22 22 22 21 8.5 8.2 8.5 6.8 July 19 9.6 21 21 21 19 8.7 8.7 8.7 6.8 July 23 8.4 23 22 22 19 8.5 8.5 8.5 6.8 July 26 5.4 24.5 23 23 21 8.7 8.8 8.6 6.8 July 30 4.7 22. 24.5 24.5 23 8.7 8.6 8.6 6.8 Aug. 2 7.6 22 23 23 20 8.5 8.6 8.6 6.8 Aug. 6 9.0 28 30 31 27 8.8 8.7 8.8 7.0 Aug. 9 1.0 25 25 24 22 8.9 8.9 8.8 7.2 Aug. 13 7.6 27 27 28 26 8.8 8.9 8.8 7.2 Aug. 15 6.9 25 25 26 24 8.2 8.6 8.7 7.2 .Aug. 20 9.0 30 30 30 27 8.8 9.0 8.9 7.2 Aug. 23 7.6 29 29 29 28 8.7 8.8 8.9 7.2 Sta. 4 Aug. 9 0.0 Aug. 13 0.0 Aug. 15 0.0 Aug. 20 0.7 Aug. 23 0.7 -.. I . 2 4 4' ~. I . u ,2 . 7 ~ _ c . I “...... y C I VA 8 t l I b , 0 J . O u 4 ‘ , . b . I 4 O I . . O ‘ ~ A . I O C no ....— DATE 1948 Mar. 28 April 15 May 2 May 16 May 31 June 14 June 28 July 3 July 8 July 15 July 22 July 27 Aug. 5 Aug. 12 Aug. 21 pH --- TEMPERATURE READINGS Station 2 pH TENT. °c 7.2 5 7.8 12 8.0 19 7.6 20 8.2 22 8.6 25 8.6 22 8.8 25 9.0 23 9.2 24 9.2 26 9.2 25 9.0 23 9.2 23 9.2 26 77 78 V. DISCUSSION OF RESULTS During the summer of 1947 the primary purpose of the survey was to determine the kinds of organisms present, and their quantity. Also general observations on limno- logical conditions of the lake water and the effluents draining into the lake were made. (pH, temperature, dis- solved oxygen). One series of samples of the lake water, inlet water, storm sewer effluent and sewage effluent was also analyzed to determine their relative content of bi- carbonates, carbonates, nitrates, nitrites and total nitrogen. During 1948, however, emphasis was placed on an attempt to determine whether a correlation existed between the quantity of organisms present and the chem- istry of the water, especially in respect to two of the inorganic forms of nitrogen, nitrates and nitrites. The chemical study will be considered in a subsequent section together with an analysis of phytoplankton cor- relation. 1. Organisms causing "water blooms" in Jordan Lake. If the arbitrary standard of 500,000 organisms per liter set by Sawyer g§_gl. (1943, 1944) is used, Jordan and Tupper Lakes are in almost continuous "bloom” condition for approximately 4 months of the year. Although great increases in number of organisms are usually referred to as "pulses” or ”blooms", in the following discussion the term l'bloom" will be used only for reference to conditions in which the phytoplankton became so abundant as to make 1' 79 the water quite turbid and somewhat colored, or when a heavy blue-green scum was present on the surface waters. Six species of blue-green algae are the main compon- ents of the "bloom" condition during the summer and early fall in Jordan and Tupper Lakes; Anabaena limnetigg G. M. Smith, Anabaeng spiroides var. crassa Lemmermann, Anabaena circinalis var. macrospora (Wittrock) de Toni, Aphanizo- ggpgg,;lgg-ggggg (L.) Ralfs, Microcystis geruginosa Kuetz- ing and Qgglggphaerium Naggglganum Unger. The periodicity of the different species of Anabaena vary in certain respects. 5, limnetica and A. circinalis var. macrospoga appeared in June and remained through summer or early fall, showing a periodicity characteristic of these species. In 1947 these two species appeared in collections as late as October 15th, whereas in 1948 they were not found after August 5th. The third species, A. spiroidgs var. crassa appeared rarely in 1947 but was very abundant beginning June 14, 1948; disappearing in August. A fourth species, A, Lemmermann;i_P. Richter also was not observed in 1947 but was found in collections during May, 1948, created a dense bloom on June 14th, and then disappeared, only to reappear in small numbers in samples taken July 15th and July 22nd. Aphanigomenon glpgrggp§§_appeared in all samples from June 24, 1947 until August 21, 1948 with the exception of a two week period in May, 1948. Coelosphaerium Naeggliangm appeared in most samples during the entire survey. This species first appeared in - I. 80 July, 1947, but became reduced in numbers or was lacking for several weeks in August, 1948 and also in March, 1948. The latter collection was taken during a flooded condition of the lake. Microcystis aeruginosa was somewhat erratic in its periodicity. During the summer of 1947, this organism was absent for a few weeks at several intervals. Col- lections in February and March, 1948 showed less than 3,000 organisms per liter of lake water. Other organisms which appeared in great abundance periodically during the study but which did not create a disagreeable condition were: Oscillatoria rubesceng_De Candolle, (another blue-green alga-); Egagilaria viresceng Ralfs; Fragilaria crotonensis Kitton; gsterionella formosa Hassall; Melosira varianstgardh and Stephanodiscug niagarae Ehrenberg (diatoms); Ceratium hirundinella (0. F. Mueller) DuJardin. Plankton samples from a southern Michigan lake contain- ing almost pure growths of Oscillatoria rubescens were collected by Dr. R. 0. Ball of the Michigan State College Zoology Department in the spring of 1948. This organism, identical with a species in Jordan Lake, gave the water a reddish purple color becguse of light refraction due to the great number of pseudovacuoles occurring in the cells. In Jordan and Tupper Lakes at certain intervals this species occurred in great abundance, but the color phe- nomenon did not appear, although specimens examined revealed presence of pseudovacuoles in the cells. 81 Diatom species listed above, present in great abundance in the June of 1947 but decidedly reduced in number the following spring, did not produce any objections able conditions other than that their preSence gave the lake water a muddy appearance. Ceratium hirundinella, a dinoflagellate, appeared sporadically in collections throughout the year. In general, this species was an important component of the summer phytoplankton, often appearing in great numbers. When other algae decline, and this species becomes very abundant, the water takes on a muddy brown appearance, due to the tremendous number of organisms which contain yellow-brown chromatOphores. In general, fewer organisms were present during the summer of 1948 than in the previous summer. The most serious condition arising from the abundance of algae occurred on August 6, 1947. At this time, the surface scum of blue-green algae was blown upon the municipal beach and.the shoreline most densely populated. The gelatinous blue-green scum became entangled with heavy mate of gladophora, and when they began to decompose, they turned a cream color and produced an obnoxious odor. Local residents were generally accustomed to the foetid odor-arising from the shallow weed beds, algal mate, a few dead fish, and other disagreeable debris that col- lected behind boat docks and in shallow coves. Neverthe- less they were quick to note this added obnoxious condi- tion and promptly started a rumor that the writer had been 82 seen "dumping" some chemical in "their" lake causing this new phenomenon. However, no treatment had been given to the lake.' Reliable local sources reported that this condition was not new to the lake and that the previous summer (1946) many tourists abruptly cancelled their stay when a similar but more serious condition occurred. In both years during July and August surface scum was intermittently present. Although not a serious offender while in the middle of the lake, such masses of vegetation served as poor advertise- ment for a resort area when washed ashore by wind and wave action, especially in the northeast end. Quantitative values for the four stations varied on the same date. Mention has been made previously of the almost complete lack of organisms entering Jordan Lake from the channel in the summer months. Dense weed beds at the mouth of the outlet of Jordan Lake (Thornapple River) made sampling in the outlet impossible during the summer months. Thus, values for Station 1 do not show the number of organisms leaving Jordan Lake, but the number of organisms in the area within the lake closest to the outlet. The importance of these weed beds, blocking the outlet, causing the phytoplankton to become concentrated and thus interfering with the determination of the quantity of organisms at Station 1 cannot be fully estimated. This may be the explanation for the high count (43,238,000 organisms per liter) on.June 24, 1947. ‘1 83 Variations in quantity at other stations also may be accounted for by the variations in current and prevailing wind direction. An example is the large count (31,464,000 organisms per liter) found at Station 6 (within Tupper Lake from Tupper Creek inlet) on June 28, 1947. At this time wind action had caused organisms to accumulate in this region of the lake. There are several points of caution to be considered when interpreting the following graphs. 1. It was possible to.make chemical analysis for N02, N03, total nitrogen and Methyl orange alkalinity at two-week intervals only (except in February and March). The possible variations in amounts of these substances present between samplings are therefore unknown. Such additional data might influence the configuration of the curves. 2. The samples for March 28 and May 16 were taken while the lake was in a flooded condition. The effect of such a condition on the water chemistry and phytoplankton quantity, both at the time of flood and for the succeeding weeks is difficult if not impossible to measure. The two samples, then merely show values for the time they were collected and only inferences may be drawn as to the effects of the flooded condition on water chemistry and plankton. 3. Temperature readings of surface lake water were usually made at about 10:00 A.M. in the morning, and thus are not indicative of temperature values throughout the 84 day. (It is well known of course that water temperatures vary but little within a twenty four hour period). 4. All quantitative determinations are indices only for the time they were taken. Several significant facts may be noted although a strict correlation between the quantity of phytoplankton and the water chemistry was not found. Chemical analysis of lake water disclose the following: 1. There is a gradual increase in pH (7.2-9.2) in the lake water as the phytoplankton increases during the sum- mer growth (see Graph). This agrees with Prescott's (1939) contention that when phytoplankton is low, pH is low and. conductivity is high. “When phytoplankton increases during the season, conductivity becomes less due to the consumption of electrolytic salts and the pH rises with the precipitation of carbonates". 2. There is an increase in carbonates and a decrease. in bicarbonates during the seasonal increase of phyto- plankton (see Graph). This is caused by the gradual increase in bicarbonates as a source of CO2 for the more abundant phytoplankton, resulting in a greater precipi- tation of carbonates. 3. Total nitrogen content, highest in February and March, varies considerably during the summer months. See Graph). This variation possibly may be accounted for not only by the fluctuations in nitrate and nitrite content, but also by the loss of NH3 as a gas through decomposition of organic material. Mortimer (1939) reports that certain ”meat 1 42 m6 31 14 62% J8 J22 A5 .21 PER FEC 85 productive lakes in England in the summer of 1938 showed less total nitrogen in the outflow than in the inflow waters, that the difference was in excess of that stored in bottom mud, and therefore represented nitrogen loss. Pennington (1942) also has showed that there was a marked loss of nitrogen from cultures of algae and bacteria, apparently indicating liberation of gaseous nitrogen. This loss may be related to the fluctuations in total nitrogen content during the summer in Jordan Lake. 4. Temperature readings of surface water showed a gradual increase from February through August. Ten read- ings as high as 30°C were made in August of 1947. 5. Dissolved oxygen content varies from sample to sample because of many factors such as temperature of water, amount of photosynthetic activity and wind action. Howb ever, values were high enough throughout the summer to support aquatic animals. One determination, that of 1.0 p.p.m. on August 9, 1947 would indicate a critical condi- tion for fish life. Inasmuch as there was no apparent fish-kill at this date the low oxygen content was obvious- ly local and peculiar to the particular area of water from which the sample was taken. 6. A general inverse correlation between the amounts of nitrites and nitrates and the quantity of phytoplankton makes its appearance, although a strict correlation cannot be drawn (see Graph). It is to be noted, however, that plankton organisms were present in the lowest quantity on May 16 and 31st, when nitrates and nitrites respectively were most abundant. And conversely, the greatest quanti- ties of organisms were present May 31 to August 21 when nitrates and nitrites were lowest. From this it may be correctly inferred that nitrogenous materials serve as nutrients for phytoplankton, and that their profuse growth had reduced the values of nitrates and nitrites accordingly. This is in keeping with the findings of Sawyer _e_1_:_ 2.1.. (1943, 1944) who found that inorganic nitrogen in Waubesa Lake was reduced from 0.95 to 0.3 p.p.m. after a "bloom“ condition. Several important factors should be considered before such an inferrence may be established as valid. Some workers, such as Pennington (1942), for example, have shown by the use of mixed algae and bacteria labora- tory cultures and simulated field conditions that algal organisms do not use nitrite but do use nitrate and ammonia, the latter much more rapidly. His experiments also showed that nitrite was produced from both ammonia and nitrate: ammonia from nitrate and nitrate from ammonia. Hence some reduction in nitrates noted in Jor- dan Lake might be related to nitrite formation and not necessarily to consumption by plankton. It is difficult to apply his results, however, to the conditions at Jor- dan Lake for several reasons. In the first place blue-green algae make up the great majority of organisms in the plankton of Jordan Lake during the summer months, whereas the cultures that Penn- ington worked with were mainly species of Scenedesmus and 89 Chlorella (green algae which are present in very negligible numbers in Jerdan Lake plankton). The physiology of these groups differ radically inasmuch as studies of Pennington (1942) and Chu (1942) have shown nutrient requirements ‘ vary greatly not only in different groups of algae but also between two species of the same genus. The increase of organisms in Jordan Lake occurred two weeks after a decrease in nitrate content and approximately at the same time the nitrite decreased. This latter sub- stance is not used directly by plankton algae (Pennington 1942, Chu 1942) and thus the rate of nitrification and ammonification appears important. The formation of nitrite from nitrate further appears probable in the May 16 to 31 period when there was a decrease in nitrate and a cor- responding rise in nitrites, (accompanied by a continued low number of organisms). The rise in quantity of organ- isms beginning May 31st and the corresponding decrease in nitrite however poses a problem and may indicate the une known value of NH}. Ammonia cannot be derived directly from nitrite (Pennington 1942) and therefore the nitrite decreased because of the formation of nitrate (and possib- ly the transfer of nitrate to NH} which is unknown here) which was immediately utilized by phytoplankton, thereby increasing the number of organisms present. This explana- tion is reasonable but definite proof is not available from such limited data. . Another factor present, which has no relationship to the inorganic nitrogen content, is that of nitrogen l'lldlfl’ll'yl 9O fixation. As previ0usly mentioned, studies have shown that certain blue-green species (dominant organisms in "water bloom" conditions in Jordan Lake), are able to fix atmos- pheric nitrogen. Sawyer 22.212 (1944) also indicate that there is accumulating evidence that nitrogen fixation is of importance in "water bloom" conditions. The importance of this factor in the Jordan Lake "water bloom" and its effect on the chemical correlation presented is not known. Inorganic phosphorous may be the limiting factor in phytoplankton ”blooms". Here, the variation in nutrient requirements by different species of algae are again important. The quantity of a nutrient present may be insufficient and limiting for one species but optimum for another. Only two series of inorganic phosphorous deter- minations were made of the water in Jordan Lake and thus the relationship, if any, between this chemical and the. quantity of phytoplankton is not established. Sawyer gt 5;. (1943, 1944) have shown that inorganic nitrogen and phosphorous are critical in the productivity of lakes, with the inorganic nitrogen limiting the amount of growth which could be produced while inorganic phosphorous con- trolled the rate at which growths occurred. Thus it is possible that the inorganic phosphorous/inorganic nitrogen ratio may be the critical factor limiting phytoplankton abundance. In general the chemistry of Jordan Lake water com- pares rather favorably to similar measurements in lakes in Wisconsin and Iowa where "water blooms" have occurred. r» ,91 (Table 1.) When only a few of the many factors that may have an effect upon algal "blooms" are compared a complete picture is not presented and therefore no definite conclusions can be drawn. An analysis shows these facts however: Jordan Lake is lower in nitrates, bicarbonates and inorganic phos- phorous (partly) and the pH is within a close range at a similar time of the year. The average number of organisms in July and August is abundant but lower than in two of the Iowa Lakes. Sawyer gt’gl. (1944) set a fertilizer threshold for the production of "blooms" by reporting ”in general, it may be concluded that lakes showing average annual concen- trations of inorganic nitrogen and phosphorous, in excess of 0.30 and .015 p.p.m., reapectively, will produce fre- quent nuisance "blooms". It is not possible to state whether the chemical conditions in Jordan Lake water per- mit the application of this hypothesis. The lack of NH3 nitrogen determinations prohibits the calculations of the total inorganic value. Furthermore, the two determinations only of inorganic phosphorous although significant do not permit conclusions to be drawn. The important fact is however, that Jordan.Lake supports a heavy "bloom" of algal organisms during the summer months whether or not its water chemistry agrees with such fertilizer thresholds as set by Sawyma £3.21. 7. Data for Station 4 (inlet) indicatex that the inlet does add nutrient materials and other important 92 .mnm m s« .mmm m :2 .mph m ed mEOOHQ msooHn msooap . mopda 000.amo.fi . ma . a cooaauosfin cooeanoefin nooauaosfin 000.m0m 000.0om 000.000.m 000.000.» manage an M .0 N H O H N m.Hm sis: ---: nan] ins: . 11:: now 0mH 0mm mmH afia H.m 0.01m.~v nus: 1:1. :11: Aw.w:s.mv ~.m H.m m.m ~.w mo msomoflbmoma maao. mflo. mg. om. . H0. H0.o H0.0 no.0 H.0 no.0 oheeaaoam mdo. mm.H moa.o mm.o $0.0 moo.o 0.0 H.o m.o H.o moz mmoaoh mammaa nmmommw emopsma esosoz spouses paamn pacemam mopsoo macaw .m:mv gamgoomaw “pmswsw use hash adv osoH .0>¢ omega szgoomHa 02a agoH a0 zomHmamsoo H earns II'I 00V... 0.1. )e f. 93 chemicals to Jordan Lake. Bicarbonates and total nitrogen values are abundant throughout most of the year at this station, whereas nitrates and nitrites become reduced in the July-August period. It is believed that although the inlet furnishes nutrients in limited amounts to Jordan Lake at certain times of the year, it is a relatively minor source of fertilizing material when compared with the storm sewer and the municipal sewage effluent. 8. The volume of flow entering Jordan Lake from the storm sewer is usually low. A large portion of the water used by the Lake Odessa Canning Company is discharged into the storm sewer. The volume and the quality varies con- siderably from day to day, as well as within a 24-hour period, depending on the volume and type of packing in process. The number of homes which empty their waste into this sewer is not known. The water that does enter the lake from this source however, is generally rich in bi- carbonates (up to 396 p.p.m.) and total nitrogen (up to 14.4 p.p.m.). The values of nitrates and nitrites (see Graph) are usually higher than those of the lake water. Although not of major importance as a source of fertili- zing materials for phytoplankton, this storm sewer, because it enters the shallow northeast end of the lake, may have an important effect on growth of aquatic plants which are very abundant in this portion of the lake. 9. The municipal sewage effluent (see Graph) is probably the major contributor of fertilizing substances .)Il]l?l ... .al. 4‘ 1.128.141 112 1116 M31 J1 827 J8 J22 A5 A21 94 mag A15 M2" 1116 M31 'J14 J2? J8 J22 A5 Afi,‘ 95 96 to Jordan Lake. The chemical content varies constantly because of the many substances entering from the village sewers. The total nitrogen value is usually 25-30 p.p.m. and the bicarbonate content is high (250-400 p.p.m.). Inorganic nitrogen content (nitrates and nitrites) is low, although higher than some values for these substances in lake water, because of the lack of aerobic bacterial action in the type of treatment plant. Despite some sludge removal, theeffluent adds many tons of organic substances to the lake which eventually may be used as phytoplankton nutrients. New additions to the municipal treatment plant are now, at the time of writing, in the planning stage. However, the inefficiency of the plant may have been res- ponsible for additional nutrient material being added to the lake and.thus have had some bearing on the abundance of organisms in the lake. Data from a survey conducted by Mr. R. G. Foster of the State Stream Control on July 9, 1947 indicate several reasons why the sewage effluent may have important bearing on the "bloom“ conditions. These data show that for a 12 hour period on July 9, 1947 the effluent from the plant was 144,000 gallons containing 1,715 pounds of total solids. Additional data are presented below in Table 2. Table 2 Raw and Final Wastes from Municipal Treatment Plant Wastes at the Sewage Plant Removal by plant Influent Effluent p.p.m. p.p.m. Total Solids 1,301 1,440 -10.7% 97 Table 2 cont. Wastes at the Sewage Plant Removal by plant Influent Effluent ' p.p.m. p.p.m. Total Volatile Solids 281 332 -ls.2% Suspended Solids 84 56 33.u% Suspended volatile solids 82 28 30.0% B. 0. D. f 265 285 - 7.5% These data indicate that although 35% of the total sus- pended solids were removed by the treatmeht plant, the total solids were higher in the treated than in the raw sewage. It is apparent that this plant has been contributing a large volume of material to the lake unnecessarily and that this material may form a large part of the bottom deposits which eventually contribute nutrients for phytoplankton use. 10. No chemical determinations were made of bottom mud samples. Jordan Lake has a thick layer of black organic bottom deposits and their importance in furnishing nutrients for phytoplankton growth cannot be over estimated. The organic matter on the bottom, derived from sources both within the lake (dead bodies of plants and animals) and from without (effluents and drainage of all types), varies in different lakes. It is here that reductions of complex organic compounds and the subsequent oxidation of these resulting chemicals into nutrient inorganic substances occur. The rate at which this transformation takes place is dependent on many factors such as the amount and type of II 98 bacteria and the content of dissolved oxygen, ferrous iron, hydrogen sulphide, ammonia and other oxidizing and reducing materials. Mortimer (1939) in England has shown that the surface layer of mud is richer in nitrates than the surface water above it, whereas in the lower mud there is active reduction and large amounts of ammonia but no nitrate. This in addition to the fact that nitrification tests are negative for the lake studied (Lake Windemere) leads him to suppose that the mud surface is the seat of nitrification. Sawyer gt,§;. (l9hh) state “that consolidated lake bottom muds which are capable of being sampled with an Ekman dredge do not appear to be significant sources of nutrient elements. However, the slurry of rapidly decom- posing organic matter which exists Just above the consoli- dated muds may be vitally important. This slurry that Sawyer gt 5;, refer to is of recent formation and the quantity present is reflected in recent productivity of organisms. The same Wisconsin studies also showed that lake bottom muds are much more stabilized than the solid matter leaving the sewage treatment plants and that sewage sludges, whether digested or not may be 10 to 90 times as productive of nitrogen and phosphorous as bottom muds. If this information can be correctly applied to the situation at Jordan Lake, then the importance of the sewage effluent even when properly treated, has a great fertilizing effect on the water of Jordan Lake, reflected in the abundant number of organisms. .3 f\ 99 The question of whether "water blooms" would continue to occur on J0rdan Lake with a diversion of the storm sewer and sewage effluent into the outlet is problematical. Tupper Lake receives no sewage effluent and yet supports as great a number of the same types of organisms in early summer as Jordan Lake does. The only inlet entering Tupper Lake is that of Tupper Greek which drains farm land and swamp areas to the northeast. The only other source of fertilizing substances entering Tupper Lake would be sewers from only several cottages and run—off from the agricultural land surrounding the lake. If these latter sources of fertilizing substances are considered minor, then the inlet or bottom deposits are instrumental in furnishing nutrients to the lake. A previously mentioned inlet (Tupper Creek) has a very reduced current, becoming almost stagnant in the summer months. Although no chemical determination of its waters are available, it seems impossible to compare the ‘small flow of Tupper Creek and its contribution of nutrients to Tupper Lake with that of the sewage effluent (over 10, 000 gals. per hr.) on Jordan Lake. Thus it might be inferred that although both sources add nutrients to the two lakes, the role of the bottom deposits is also import- ant in producing similar quantitative plankton (at least in early summer). Both lakes can be classified as eutrophic (productive). Among some of the characteristics of this type of lake, are a high quantity of phytoplankton with blue-green algae and diatoms predominating and usually a bottom deposit of 100 organic matter in which a vigorous putrefaction takes place. Hasler (19MS) has shown that domestic drainage and sewage have changed.many lakes (both in Eur0pe and America) into eutrophic types. This is accompanied by the building up of rich organic deposits on the bottom. A similar condition of eutrophication in Jordan and Tupper Lakes may have occurred where sewage and other drainage have built up bottom deposits and the accessory high production. The abundance of organisms in Tupper Lake is no doubt related to its sources of fertilizing substances which are: l. Tupper Creek. 2. Wash-off from surrounding farm land and swamps. 3. Organic matter in bottom deposits and in suspen- sion in lake water. #. Minor contributions from few cottages and inhabi- tants. The great amount of phytoplankton in Jordan Lake is related to the follOWing sources of fertilizing substances: 1. Inlet (channel from Tupper'Lake) 2. Storm sewer. 3. Sewage Effluent. M. Organic matter in bottom deposits and in-suspension in lake water. 5. Drainage from surrounding terrain. 6. Possible sewer connections from homes and cottages. 7. Debris and wastes contributed by the many people who use the lake for recreational purposes. This study has been limited of necessity to a general 101 consideration of a complex problem, with special emphasis on the relationship of nitrate, nitrite and total nitrogen to "water bloom" conditions at Jordan Lake. It has been impossible to take into account all the factors related to I'bloom" conditions. many otherfactors (listed below) such as those advanced by Hutchinson (l9hh) have been little studied. a. Inorganic nutrients other than P, N and Si. b. Specific organic substances. 0. The physiological condition of plankton organisms at different stages of their cycles of growth. d. Competitive relation between different species of phytoplankters. These are only a few of the many other aspects of phytoplankton periodicity that may be important and readily indicate the need for continued and diversified research before a complete solution is possible. It is appropriate to summarize this discussion of data with a quotation from Hutchinson (l9hh). “We should expect, from the results of laboratory experiments, to find that conditions in nature are extremely complex and difficult to analyze, and this is indeed the experience of every investigator of phytoplankton of lakes.” 102 VI. TREATMENT AND CONTROL A. Types of Treatment Other Than Copper Sulphate Previous mention has been made to several papers and publications relating to control of algae and to harmful effects produced by them in lakes and reservoirs. Since the early nineteen-hundreds water-works engineers, faced with the important problem of furnishing clean and pure water to the public, have treated water reservoirs and other sources of public water supplies for algae control, using both physical and chemical methods. Physical methods include: 1. Dredging back shorelines to deepen the water and to maintain steep sides. 2. Artificial aeration. 3. Inlets to promote circulation. h. By-passing water when objectionable algal growths are present. 5. Removal of mud by periodical cleaning of reservoirs. 6. Building reservoirs so long axis may benefit from prevailing wind action. 7. Removing nitrogen and phosphorous from inflowing waters. 8. Stocking with fish to reduce plankton. 9. Building covered reservoirs. Some of the above procedures have been applied with 103 success in certain places, but the vast majority of water- works engineers use some type of chemical treatment. Reports such as Manguin (1928, 1930) report success- ful algal control by chlorination up to 1.0 p.p.m. Whipple (1927) reports use of chlorine as an algacide in England by Houston and by Hale in 1921 in New York. Chlorine, whether added in excess of the quantity demanded to kill organisms or not, may serve as an additional purpose by eliminating tastes and odors. Some reservoirs are treated with CuSOh for killing the organisms, and then with chlorine to remove odors and tastes. In turn, the chlorinous taste sometimes has to be removed by dechlorination with such chemicals as sulphur dioxide, sodium sulphite, bisulphite and thiosul- phate and activated carbon. Arnold (1936) reports that chlorine is a fairly effective algacide and has proved effective as long as a chlorine residual was maintained. Being a gas of low solubility, chlorine is difficult to apply without expensive equipment and must be handled in heavy containers. Chloramine is used sometimes with suc- cess at certain localities but often CuSOu in combination is needed (Bailey, 1937). The use of chloramine results in a more persistent residual chlorine but leaves free NH3 for plant growth. Arnold (1936) indicates that this combina- tion of chlorine and NH3 is used in California waters for eradication of Corophium, a fairy shrimp, but not for algae control. Another chemical combination of chlorine, "bleach- ing powder“ or calcium hypochlorite, a solid compound with 10h 30 percent available chlorine when dissolved, is sometimes used. Kienle (1932) reports the successful use of dry calcium hypochlorite in Boston, Massachusetts and Wilming- ton, Delaware. Other chemicals have been used as a alga- cide or for taste and odor removal, or for both purposes. Whipple (1927) indicates that potassium permanganate may be used for eradication of tastes and odors. It does not retard chlorine action, but assists in sterilization. This chemical is one of the constituents of a product used by one of the commercial companies for elimination of algae in swimming pools (Perkins, 1946). The chief objections to potassium permanganate are the tendency to render chlor- inous tastes more pronounced and the persistence of a pink or even brown color if ground or colored waters are treated. Use of commercial products such as Perkins CM-2l usually has been restricted to swimming pools. Other alga- cides such as Benoclor~3 have been reported to be success- ful in reducing algal and other aQuatic plant growth. This chemical, however, imparts a noticeable taste to the water which may last as long as 33 days (Gibbons, 19h0). B. Copper Sulphate, Its Use and Objections to Use. Copper sulphate has been the most economical and one of the most efficient chemicals used by the sanitary engine eer in water supplies. In most cases, this chemical has been employed successfully, sometimes in conjunction with chlorine or some other taste remover. One of the reasons why cOpper sulphate is chosen over some other effective 0'. (0 (0 O n! . ,. . \.'\ 7 105 chemicals, is the ease with which it can be applied. Several methods are used for application. The main ones are as follows: 1. Dragging burlap bags containing crystals behind boats. 2. Spreading finely powdered CuSOu on ice or on water by hand or by special equipment. 3. Continuous dry feeding in situations where there is a narrow and controlled inlet to a reservoir or aqueduct. h. Spraying the desired percentage concentration in solution from a tank mounted on a barge or boat. This appears to be one of the most popular and effective methods, as it insures more even distribution of the solution. This method also has an added advantage in that the solution diffuses as it sinks, and thus comes in contact with the maximum amount of vegetation. This is especially good for Aphanizomenon and Microcystig which float on or near the surface. Although demonstrated to be effective and econom- ical (some lakes have been treated for as low as $0.63 an acre), the chief objections raised to the use of copper sulphate as an algacide are as follows: 1. Possible injurious effect of copper sulphate in water supplies for commercial and domestic consumption. Hale and Muer (1926) however found that no copper of sani- tary significance could be found in the New York City water distribution system after watershed treatment with c0pper sulphate. Hale (1930) reports that copper salts have no effect on the health of individuals using water from public 106 supplies which have been treated with copper sulphate. 2. The effect of 00pper sulphate on fish life and fish-food organisms. Numerous articles report fish-kill after copper sulphate treatment. Smith (l92fl) discusses one case and lists 18 fish—kills out of 38 treatments. M. W. Smith (1936) reports the use of copper sulphate for eradicating predatory fish populations of a lake. In this case a concentration of 3 p.p.m. was used. After 1 hour, the cOpper content was 1 p.p.m. but later it was 2.h p.p.m. and 9 months later bottom waters contained 2 p.plm. The phytoplankton was almost entirely destroyed and growth was low for a year. Zooplankton was also almost completely destroyed. Leeches lived, but most of the fish and even eels were destroyed. Titcomb (191%) also discusses the use of c0pper sulphate for the destruction of obnoxious fish in ponds and lakes. Schoenfeld (l9h7) notes that Lake Monona near Madison, Wisconsin has almost a sterile bottom condi- tion after 20 years of treatment with this chemical. He further says that there are only 700 bottom organisms per square yard in Lake Mendota, a connected lake nearby that has never had copper sulphate treatment. Lake Nonona also has 605 units of c0pper on the bottom, whereas in nature Lake Mendota has 85 units. Thorpe (19h2) claims that copper sulphate treatments destroy some of the intermediate organisms composing the food chain and the fact that such treatments usually do not kill fish is irrelevant. He examined a lake treated 107 for control of algae, (for 16 years) in which, despite heavy stocking and other management efforts, there had been a reported general decline in fishing success. Basic fertilizers in this lake were average in amount but bottom organisms were very reduced in numbers. He also notes that continued treatment had changed the quality of algae annually present and that those now present are sure resist- ant to treatment but equally obnoxious. There are many proponents of copper treatment in natural waters where the problem of fish life is involved. Domo— galls (1935) reports that lakes may be treated without injury to weed beds, zooplankton and fish-life. Prescott (1932, 1938, 1948) maintains that when applied correctly copper sulphate can be used in such minute concentrations that it is not injurious to fish life. Aitken (1933) while trying to eliminate certain fish (Black bullhead, black striped shiner, and green sunfish) used concentrations of as much as 7,500 parts per million gallons of water and failed to kill these fish even after RS hours. Eventually chlorinated lime (1 lb. per 2,000 gallons) was successful in 29 minutes. Rushton gt_§l. (1924) report that treatments of .05 p.p.m. sprayed on three successive days for a total of 0.15 p.p.m. were able to reduce Coelastrum from h,576 to 68 per cc. in 7 days but "neither were adult trout, trout fry, nor the crustacea, Qaphnia, staple food of the young trout affected by treatments". As previously mentioned Smith (192h) notes that many fish-kills were due to the depletion of oxygen by the decomposition of algae killed by copper sulphate and 108 not by copper sulphate itself. The basic contention of those who favor this type of treatment is that cOpper sulphate when used judiciously can be effective in treatment of algal nutsances and yet be harmless to the fish life of a lake or reservoir. In regard to killing of fish food, the opinion is that when used carefully, CuSOu will control the algal nuisance but will destroy only such a small portion of the available fish food organisms, thus there are no damaging effects to fish productivity. Table 3 shows concentrations of copper sulphate recommended for treatment of algae. Table h shows concentrations of copper sulphate used and found to be safe for different types of fish. It will be seen that some of the concentrations required for the destruction of certain algae are close to those which have been found deadly to fish, thus extreme caution should be used. Because each lake or reservoir has its own individual characteristics, it is necessary before c0pper sulphate treatment is administered, that the following factors be taken into consideration: I l. The type or types of algae present and their quantity. This is very important because certain algae can be eliminated by specific dosage. Quantitative exam- ination of algal life in a lake will indicate when organ- isms approach a nuisance condition and indicate when treat- ment must be given to be the most effective. Many treat- ments have been unsatisfactory because they were not given at the proper time. I! TABLE 3 109 Concentrations of COpper sulphate recommended for treatment of algae in lakes and reservoirs. ORGANISMS COPPER SULPHATE ORGANISHS COPPER SULPHATE (parts per million) (parts per milliom Myxophyceae Xanthophyceae Aphenizomenon 0.2-0.H Botryococcus 0.22 Anabaena 0.2~0.h Tribonema 2.0-0.h Microcystis O.2-O.h Rivularia 0.1 Cryptophyceae Synura 0.33 Chlorophyceae Uroglena 0.08-0.25 Hydrodictyon 0.1 Mallomonas 0.5 Eudorina 10.0 Pandorina 10.0 Diatomaceae Scenedesmus 0.1 Melosira 0.2 Stephanodiscus 0.33 Synedra 0.36 (after Prescott (1938) TABLE n Concentrations of copper sulphate that have been used safely for fish. FISH COPPER SULPHATE REFERENCES (parts per million) Trout 1.0 Anonymous (1904) Trout (fry) 2.0 Marsh & Robinson (1910) Trout (brook) 0.6-0.8 Trout (brook, fry) 1.0 " ” Trout (brown) 0.6-0.8 " " Trout (rainbow) 0.6-0.8 " ' Sunfish 1.2 Kellerman (1912) Sucker 0.3 " Pickerel 0.- " Perch (yellow) 0.5 Marsh & Robinson (1910) Perch 0.75 Kellerman (1912) Black bass (small) 2.1 Black bass (large) 5.0 Marsh & Robinson (1910) Carp 0.£ Kellerman (1912) Gar Pike 0. 6 Prescott (1938) Sheepshead 0.u6 " Catfish 0.28 " Blue” 1‘11 00 6 N Bass silver) 0.h6 " Q - ~ . ._— . . . - . . o - - — .. l I _ . . h _ .- .. A ‘1. o— .. v - , ,_ . . . 4 . i - - r - a . . , - n _- . .— ~ 110 2. The volume of water must be calculated so that the amount of copper sulphate required to produce the proper concentration for an effective dosage can be determined. 3. Temperature. More 00pper sulphate is necessary in colder water. Dosages recommended are usually for 15 degrees Centigrade (59 degrees F) and several authors (Goudey 1936, Gopp 1936) suggest adding or decreasing 2.5 percent of cOpper sulphate for every degree of variation from 15° C. h. The alkalinity of the water must be determined becaus e the more alkaline the water the greater the amount of copper sulphate required. A 0.5 to 5.6% increase for each 10 p.p.m. alkalinity is recommended. his is due to the fact that copper sulphate dissociates into Cu and SO which react: with carbonates to form copper carbonate and calcium sulphate with some liberation of carbonic acid. Copper carbonate then breaks down and forms (fig-Eggs!) hydrate (by union with OH ions) which is insoluble and precipitates out. The greater the alkalinity, the greater the amount and more quickly does the copper hydrate settle out. 5. Technique of treatment. The most effective and safest method is by spraying. Not only does this method insure more copper coming in contact with the growth, but it also makes possible a better control over the concen- tration used. The drag method (that in which the crystals in a burlap bag are towed through the water) has been responsible fer the death of fish in many treatments 111 because of the heavy concentration of cOpper sulphate created in a narrow zone through which the bag passed. Many of the older treatments were made this way and may be responsible for the fish deaths in the cases listed by Smith (1924). Six of the 18 cases of death involved a concentration of 10 p.p.m. or over of copper sulphate. The control of algal nuisances by copper sulphate in waters containing fish continues to be a problem to the various workers in the fields of aquatic biology. Such control should serve a two-fold purpose: 1. To produce no objectionable affect on fish pro- duction. 2. To control obnoxious conditions, to benefit water supplies and to provide enjoyable recreational sites. If the opponents of the capper-sulphate treatment can successfully prove their contention that this method severely interfere with fish production, then other means of control are necessary. Other suggested methods of control are: l. Plantings of species of fish (such as the golden shiner and gizzard shad) which use considerable algae in their diet. This method may be of some use although a completely satisfactory solution is doubtful. The blue- green algae that produce some of the most severe "water blooms“ appear to be a very minor source of food to any type of fish. 2. Planting of water plants with broad floating leaves which shade the water and restrict the growth of /- 112 algae. This method may be somewhat successful along shallow margins of lakes but such plants do not survive in deeper water where phytoplankton may be abundant. 3. Introducing of crayfish which inhibit growth of vegetation by filling of water thus reducing light penetra- tion. This does not appear practical in a large body of water. ’ M. Removal of nutrients entering bodies of water. This possibly could be done for small lakes where household sewage, barnyard drainage and a small amount of wash—off from agricultural land occurred, but not practical for large drainage takes where rivers or other large effluents contribute nutrients. This also ignores the role of bottom deposits which may be important contributors of nutrients to "water bloom" organisms. Some work has been done on the removal of nutrients from sewage effluents entering lakes. Sawyer gt 91. (l9hh) have shown ferric chloride when used as a coagulant removes the majority of phosphorous and organic nitrogen but not inorganic nitro- gen from effluents. It was also shown that glucose reduces a large pro- portion of inorganic phosphorous and nitrogen but not total nitrogen in effluents. Whether an economical and practical application of these methods can be employed where sewage plays a dominant role as a fertilizing substance in "water blooms" is not known. Complete diversion or elimination of sewage effluents entering lakes and other bodies of water may also aid. 113 5. Thorpe (l9u2) believes that it may be possible to control types of algal organisms by adjusting basic fertil— izers in lakes so as to inhibit the growth of objectionable forms and at the same time promote less bothersome ones. This is only theoretical and no research of this nature has been done. 6. The discovery of a chemical, which could be used for specific elimination of objectionable forms of algae without being injurious to all other aquatic life. C. Treatment Of Jordan Lake Although original plans provided for copper sulphate treatment in Jordan Lake applications of this chemical were not made for the following reasons: 1. The only condition severe enough to justify treatment occurred on August 6, 19u7. The algal growth made a sudden appearance and by the time arrangements for treatment were made, conditions were beginning to clear up. 2. Fear of fish loss by resort owners. This was in part engendered by the appearance in a current popular Sportsman's magazine of an article condemning the use of capper sulphate in lakes, and in part to the fear that results of the treatment might deprive them of business. 3. The thought held by local people that the bacter- ial pollution problem was related to the "water bloom" and that additions to the municipal sewage plant, required by the State Stream Control Commission, would eliminate the great number of organisms when installed. 11h h. The majority of people who use the lake, do so for .fishing and the scum condition is not too objectionable to them. Relatively few peOple used the lake for swimming purposes in the summer of 19H? because of the pollution condemnation hence there was little demand for a clean lake. In any case during the summer of l9u8, the condition was not as serious as previous years. D. Brighton Lake and COpper Sulphate Treatment Although the effect of treatment could not be studied at Jordan Lake, a similar "water bloom" condition on a lake near Brighton, Michigan permitted observations on the use of copper sulphate. This treatment (supervised by Dr. G. W. Prescott) was made during the summer of l9h8. This lake, not known by a formal name,is situated almost entirely on land owned by Howell Memorial Boy Scout Reservation about one mile southeast of Brighton, Hichigan. This lake is in part an artificial body of water, the result of damming of a small drainage stream approximately 20 years ago. The circumference of the lake is just under 2 miles and.the area occupies nearly 10 million cubic feet, of which over half is water from 9-3 feet in depth. The margins are shallow, supporting a large growth of submerged aquatic vegetation. The inlet is at the northwest, and carries the municipal sewage effluent from the city of Brighton. The southwest bay of the lake covers a "pot hole“ about 30 feet deep which existed as a pond separate from the creek before it was dammed. 115 This body of water is used for fishing, boating but primarily for swimming by about 500 Scouts on the reserv- ation during the summer. In the summer of l9h7 (and ' previously) a severe "water bloom" made swimming impossible. R. C. Busby, Director of Camping and Activities Ser- vice for the Detroit Council of the Boy Scouts of Amefiica arranged with Dr. G. W. Prescott in May 19MB, that the lake be given cOpper sulphate treatment. Examination of plankton tows taken May 2hth showed the presence of organisms (mainly diatoms similar to those occurring in Jordan Lake at the same time). An exception was Dinobyon sertularia Ehrenberg, a member of the Chryso- phyta, the presence of which in large quantities imparts a light brown muddy appearance to the water. The total number of organisms on this date was 110,000 per liter. A heavy "bloom" developed on June 13th and a sampling revealed an entirely different picture. The quantity of organisms had increased to 2,907,000 organisms per liter and consisted of three identical species of blue-green algae that produce "bloom" conditions in Jordan Lake. They were Anabaena limnetica C. m: Smith, Anabaena circinalis var. macrospora (Wittrock) De Toni and Aphanizomenon giggrggggg (L.) Ralfs. Their abundance imparted a bluish-green color to the water in sharp contrast to muddy appearance of the water three weeks previously. A 5% solution of copper sulphate (calculated to give a concentration of l p.p.m.), was administered in the north- western part of the lake, by spraying from a tank mounted 116 on a barge. This area is the most shallow and was clogged at that time with masses of submerged aquatic plants. Adding to the disagreeable conditions caused by the blue- green algae were floating mats of Hydrqdigtyon relipulatum (L.) Lagerheim which covered a large portion of the water. This treatment proved ineffective as samples, taken two days later on June 2Mth, showed a great increase in algal organisms. The total count was 10,146,000 per liter and was composed almost entirely of Aphanizomenon, with lower numbers of Anabaena. At this time another treatment of the same concentration (1.0 p.p.m.)_was administered to the northeastern portion of the lake. Examination of quantitative samples five days later (June 29th) showed a great decrease in organisms. Aphani- zomenon had declined from 9,26l,h90 to 487,120 per liter and the filaments of this species which were present occurred as short broken and partly deteriorated segments. Anabaena decreased from 691,150 to 3M7,0MO per liter and were in similar broken condition. The effectiveness of the treatment was further shown, as the sample on July 7 was very clear, with very small numbers of organisms, the count being below 2,000 per liter. A qualitative sample on July 21 showed a slight increase in growth of diatoms and motile Chlorophyceae but no blue- green algae were present. A quantitative sample seven days later (July 28) indicated continued increase of diatoms, especially Melosira which occurred 206,000 per liter. This same sample also 117 revealed the presence of a great number of Daphnia, a Cladoceran, indicating that the treatment had reduced the blue-green algae, but had not completely destroyed the zooplankton. A final examination of the water on August 11th showed one species of Anabaena had reappeared in limited number and that the rest of the phytoplankton was composed mainly of diatoms. The treatments of the lake permitted complete use of the swimming beach on the southeastern shore of the lake throughout the period studied. After the general treat- ment on June 24th only local portions of the lake such as the bathing beach area were sprayed, several administrations, using the same concentration of COpper sulphate, being necessary. There were no fish killed at any time during the period of treatment in the lake at Brighton. I‘ 118 VII. CONCLUSIONS 1. Six species of blue-green algae are the major compon- ents of the ”water bloom“ occurring in Jordan Lake during the summer months. They are: Anabaena circinalis var. macrgspora (Wittrock) De Toni, Anabaena spirqides var. crassa Lemmermann, Anabaena limnetica G. M. Smith, Aphanizgmenon flggrgggg§_(Linnaeus) Ralfs, Miggggystis ggggginosa Kuetzing, Coelosphaerium Naegelianum Unger. These organisms form obnoxious scums because of their ability to multiply rapidly, their tendency to float on or near the surface of the water because of the presence of pseudovacuoles, and the tendency to adhere together in clots or scums resulting from the presence of sticky gelatinous or mucilaginous sheaths. 2. A general correlation seems evident between the number of organisms present and several factors in water chem— istry, although a strict correlation does not exist. a. A general inverse correlation exists between the total number of organisms and the amounts of nitrates and nitrites present in lake water indicating the use of these substances as nutrients either directly or indirectly by the algae. b. There is a gradual decrease of bicarbonate and an increase in monocarbonate content of the water because of the utilization by algae of bicarbonates as a source of carbon dioxide during the summer. There is a corresponding 119 rise in pH as a result of the precipitation of carbonates. 3. The inlet to Jordan Lake, the storm sewer and the municipal sewage effluent are the major sources of fertil- izing substances entering the lake. The rich productivity of Jerdan Lake may be explained (at least in part) by the great amount of organic matter in the bottom deposits. Minor sources of fertilizing substances are the disposed-of household sewage directly into the lake and the depositing of waste materials by the persons who use the lake for recreational facilities. h. The use of COpper sulphate for control of the algal nuisance at Jordan Lake was withheld because of reluctance of local inhabitants. Treatment of a similar condition at a lake near Brighton, iichigan showed that the obnoxious growths of blue-green algae could be controlled without any apparent injury to fish-life. 5. Physical, chemical and biological data and their analyses are presented for the period of June 2h, 19h? through August 21, l9us. 6. The place and mode of wintering over is not completely known. Aphanizomenon flos-aquae (L.) Ralfs in vegetative condition is present throughout most of the year although resting spores (gonidia) are produced by this species. Anabaena species also produce resting spores which are thought to winter over in the mud and debris of aquatic vegetation near shore. Microcystis aeruginosa Kuetzing and Coelosphaerium Naegelianum Unger are thought to winter over 120 as dormant single cells in mud and debris. 7. The "bloom" conditions in Jordan Lake could be control- led temporarily by treatment of copper sulphate with the Spray method. Microscopical examination by an experienced aquatic biologist would indicate the time for proper treat— ment. Permanent measures which would alleviate and possibly reduce "water blooms" would include: a. Diversion of the municipal sewage effluent. In order to eliminate the major source of fertilizing substances entering the lake, the effluent should be dischar- ged into the outlet. The lake has a very deep bottom in the southwestern area of the lake, according to local information. The effluent could be discharged into this deep part of the lake (50-60 feet). This would place the nutrient bearing water of the effluent in a cold zone where overturn would be slow or negligible. This does not mean that none of the fertilizing substances would ever get back into circulation and into a condition usable by plants, but it would detract enormously from the fertilizing influence of the sewage effluent. It should be emphasized that any- thing at all that can be done to eliminate fertilizers in the lake would contribute to a lessening of the algal nuisance. b. Improvements and additions to the sewage treatment plant. The present facilities permit the entrance of a greater amount of solids to the lake than is necessary. 0. Removal of all other sewage lines (if present) 121 from storm sewer connections. d. Removal of all sewage lines emptying directly into the lake from lakeside homes and cottages. e. Elimination of the practice of dumping garbage and other wastes into the lake. f. Dredging back shallows and beaches where algae become especially objectionable. 8. A systematic list of the algae in Jordan Lake and illustrations of them are presented. 122 VIII. SYSTEKATIC LIST OF ALGAE IN JORDAN LAKE Phylum CYANOPHYTA Class CYANOPHYCEAE Sub-class A. CHROOCOCCEAE Order I. CHROOCOCCALES Family Chroococcaceae Chroococcus Naegeli 1849 l. Chroococcus dispersus (v. Keissler) Lemmermann Smith, 1920, p. 28, P1. 1, Fig. 2. Diameter of cells 3-4 u. Pl. 1, Fig. l. Plankton tow. May. 2. Chroococcus limneticus var. carneus (Chodat) Lemmermann Smith, 1920, p. 30, P1. 1, Fig. 6. Diameter of cells (without sheath) 7 u; with sheath 9 u. Pl. 1, Fig. 2. Plankton tow. May. 3. ghgpococcus minutus (Kuetzing) Naegeli Smith, 1920, p. 28. Pl. 1, Fig. 1. Diameter of cells without sheath 6.h5 u; with sheath 8 u. Pl. 1, Fig. 3. Plankton tow. May. Merismopedia Meyen 1839 l. Merismopedgg tenuissima Lemmermann Smith, 1920, p. 33, Pl. 2, Fig. 2. Diameter of cells without sheath 2 u. Pl. 1, Fig. A. Scrapings from stem of aquatic plant. August. 123 Hicrocystis Kuetzing 1833 l. Microcystis aeruginosa Kuetzing Smith, 1920, p. 39, Pl. 5, Figs. 2-3. Diameter of cells u-u.3 u. Pl. 1, Figs. 5-6. Common in summer plankton, often forming a heavy growth. 2. Microcystis aeruginosa var. mgjg£l(Wittrock) G.M. Smith Smith, 1920, p. no, Pl. a, Fig. 6.' Diameter of cells 5-6 u. Pl. 1, Fig. 7. Summer plankton. Aphanothece Naegeli 18M9 l. Aphanothece stagnina (Sprengel) A. Braun Smith, 1920, p. 45, P1. 6, Fig. 2. Diameter of cells n u; length 3-6 u. Pl. 1, Fig. 9. Common in summer plankton. Sub-class B. HOREOGONEAE Order HORMOGONALES Sub-order HOMOCYSTINEAE Family Oscillatoriaceae Spirulina Turpin 1827 1. Spirulina mgjg£_Kuetzing Smith, 1920, p. 50, Pl. 7, Fig. l. Trichomes 1-2 u. in diameter. P1. 1, Fig. 10. Plankton. May. Arthrospira Stizenberger 1852 l. Arthrospira Jenneri (Kuetzing) Stizenberger Tilden, 1910, p. 85, Pl. n, Fig. nu. Trichome 6.U5 u. wide; cells 7-8 u long. Plankton tow. June. Mixed in filamentous mat along shore. 2. Oscillatori Vaucher 1803 Oscillatoria Agardhii Gomont Geitler and Pascher, 1925, p. 369, Figs. Tilden, 1910, p. 62, Pl. n, Fig. 2. Trichome u.3 u wide; cells 3-3.5 u long. Oscillatoria amohibia Agardh 12% P1. 1, Fig.11. k55-u56. Pl. 1, Fig.12. August. Geitler and Pascher, 1925, p. 36%, Fig.h3l. Trichome 3 u wide; cells n u long. P1. Blue-green film on bottom. August. 3. Osggllatggggchlorina Kuetzing Geitler and Pascher, 1925, p. 361. Tilden, j. 1910, p. 75, P1. h, Fig. 22. Trichome 4 u wide; cells 5 u long. P1. Plankton. February. A. Oscgllatorgg formosa Bory Geitler, and Pascher, 1925, p. 372, Fig. Tilden, 1910, p. 80, Pl. h, Fig. 33. Trichome 8.6 u wide; cells 2.5-3 u long. Blue-green growth on bottom. August. 5. Oscillatoria limnetica Lemmerman Geitler and Pascher, 1925, P. 365. Pres 1, Fig. 13. 1, Fig. 1%. h6h. P1. 1, Fig.15. cott, 19M9, 124 p. 753, P1. 109, Fig. 17. Trichome 1.5-1.8 u wide; Pl. 1, Fig. 16. Blue-green film on bottom. August. 6. Oscillatoria limosa Agardh Tilden, 1910, p. 65, Pl. h, Fig. 6. Trichome 12-lh u wide; cells h-h.3 u long. P1. 1, Fig. 17. Filamentous mass along shore. August. 7. Oscillatoria princeps Vaucher Tilden, 1910, p. 62, P1. 9, Fig. 3. Trichome 3—4 u wide; cells 3.5-7 u long. Pl. 1, Fig. 20. Plankton tow. Kay. 8. Oscillatoria rubescens De Candolle Geitler and Pascher, 1925, p. 36, Fig. #47. Cells 6.5 u broad, 3-M u long. Pl. 1, Fig. 18. Common in plankton. Winter and spring. 9. Oscillatoria sancta Kuetzing Tilden, 1910, p. 64, P1. 4, Fig. 5. Trichome 10.75 u wide; cells 2 u long. Pl. 1, Fig. 19. In mat of filaments attached on bottom. August. 10. Oscillatoria solendida Greville _Tilden, 1910, p. 76, P1. h, Figs. 23-25. Trichome 3 u wide; cells 5 u long. In blue-green mat on bottom. August. 11. Oscillatoria tenuis Agardh Tilden, 1910, p. 1, P1. h, Figs. 17-18. 125 Trichome 6-7 u wide; cells 2-3 u long. Pl. 1, Fig. Phormidium Kuetzing 1843 1. Phormidium mucicola Nauman and Huber-Pestalozzi Nauman and Huber-Pestalozzi, 1929, p. 67; Prescott (manuscript), pl. 111, figs. 4-5. Cells 1.3-2 u in diameter, 1.8-3 u long. Endophytic in giprocystis aeruginosa Kuetzing. Common in summer. 2. Phormidium Retgii (Agardh) Gomont Tilden, 1910, p. 102, P1. 5, Figs. 1-4. Trichome 4-5 u wide; cells 5-6 u long. Pl. 1, Fig. 22. Scrapings from concrete culvert at storm sewer entranceto lake. October. Lyngbya Agardh 1824 1. angbga aerugineo-caerula (Kuetzing) Gomont Tilden, 1910, p. 116, P1. 5, Figs. 32-33. Trichome 6.6 u wide; cells 3-6 u long. Pl. 1, Fig. 23. Scrapings from stem of aquatic plant. August. 2. Lyngbya aestuarii Gomont Tilden, 1910, p. 120, P1. 5, Figs. 40-41. Trichome 8-11 u wide; filament 12-15 u wide; cells 3-6 u long. P1. 1, Fig. 24. Washings along shore and mixed in floating mats. August. 3. Lyngbya Birgei G. M. Smith Smith, 1920, p. 54, Pl. 7, Figs. 14-15. 126 Trichome 21 u wide; cells 2-5 u long. pl. 1, Fig. 25. Summer plankton. Not common. 4. angbza epiphytica Hieronymus Geitler and Pascher, 1925, p. 397; Prescott, (manu- script), Pl. 112, Figs. 2-3. Trichome l-l.5 u wide; cells 1-2 u long. Pl. 1, Fig. 28. Epiphytic on Tolypothrix lgnata (Desvaux) Wartmann. August. 5. gyngbya Hieronymusii Lemmermann Fremy, 1930, p. 197, Fig. 192. Trichome 15-17.2 u wide; sheath 1 u wide; cells 2.5- 3.4 u long. P1. 1, Fig. 26. In washings along shore. Aug. 6. angbxa penicillata Kuetzing Tilden, 1910, p. 115. Trichome 4.5-5 u wide; cells 6-11 u long. P1. 1, Fig. 27, Scrapings along shore. June. fiicrocoleus Desmazieres 1823 1. Hicrocoleug_pgludosus (Kuetzing) Gomont Tilden, 1910, p. 158, P1. 6, Fig. 30. Trichome 5 u broad. P1. 1, Fig. 29. Mixed in fila- mentous mass along shore. June. Sub-order HETEROCYSTINEAE Family Nostocaceae Anabaena Bory 1822 1. Anabaena circinalis var. macrospora (Wittrock) De Toni. 127 Smith, 1920, p. 60, P1. 9, Fig. 6, P1. 10, Fig. 1. Cells 8-10 u broad; heteroCysts 8-10 u broad; spores 12 u broad, 20 u long. P1. 1, Fig. 30. Common in summer plankton. A component of surface scum in Aug. and Sept. 2. Anabaena cylindgigg Lemmermann Geitler, and Pascher, 1925, p. 328. Cells 3-4.5 u broad; heterocysts 4-6.45 u broad, 6- 10 u long; spores 4 u broad, 15-17 fl long. P1. 1, Fig. 31. Beach pool. May. 3. Apabaena Lemmermangii P. Richter Smith, 1920, p. 61, P1. 10, Fig. 8, P1. 11, Fig. 1. Cells 5-6.45 u broad, 5-6 u long; heterocysts 7 u long; spores 13 u broad, 28-32 u long. P1. 2, Fig. 1. Common in plankton. May. 4. Anabaena liggetica G. M. Smith Smith, 1920, p. 57, P1. 8, Fig. 3. Cells 8-9 u broad; heterocysts 10 u broad; spores 17 u broad, 24 u long. P1. 1, Fig. 32. Common in summer plank‘ ton. A component of surface scum in July, Aug. and Sept. 5. Anabaena oscillarioides Bory Geitler, and Pascher, 1925, p. 326. Prescott, (manu- script) Pl. 117, Figs. 8—10. Cells 6.5 u broad, 3.5 u long; heterocyst 7.9 u broad, 8-9 u long; spores 10-11 u broad, 23-24 u long. P1. 1, Fig. 33. In debris, beach pool. May. 128 6. Anabaena spiroides var. crassa Lemmermann Smith, 1920, p. 59, P1. 9, Figs. 103. Cells 9-10 u broad; heterocysts 12-14 u broad. Pl. 1, Fig. 34. Common in summer plankton. A component of sur- face scum in July, August and September. Nostoc Vaucher 1903 l. Epstoc microscopicum Carmichael Tilden, 1910, p. 176, P1. 8, Fig. 5. Cells 4.3 u broad; heterocysts 6 u broad. P1. 2, Fig. 2. Among washings along shore near inlet. June. 2. Nostoc paludosum Kuetzing Tilden, 1910, p. 165, P1. 6, Fig. 38. Cells 3‘u broad; heterocysts 3.5 u broad. Pl. 2, Fig. 4. Fixed with other filamentous algae in beach pool. May. Aphanizomenon Morren, 1838 l. Aphanizomenon flggyggggg,(L) Ralfs Smith, 1920, p. 61, P1. 11, Figs. 2~4. Cells 4-6 u broad; 6-14 u long; heterocysts 5-7 u broad, 6-18 u long; spores 6—8 u broad, 30-80 u long. P1. 2, Figs. 3 and 4. Common in summer plankton. An important constituent of ”water bloom". Cylindrospermum Kuetzing 1843 1. Cylindrospprmum ggagnale (Kuetzing) Bornet and Flahault Tilden, 1910, p. 198, P1. 10, Fig. 2. Cells 3.3-4 u broad, 4-8 u long; heterocysts 5 u broad, 8.6 u long; Spores 10-16 u broad, 32—40 u long. P1. 11., 129 Fig. 6. Attached to grass and leaves in shallow beach pool. June. Family Scytonemataceae Tolypothrix Kuetzing 1843 1. Iglxpothrix lanatqp(Desvaux) Wartmann Tilden, 1910, p. 230, P1. 14, Fig. l. Filaments 10-15 u broad; trichomes 9-10 u broad; heterocyst 10-11 u broad. P1. II., Fig. 7. Attached and floating masses along shore. August. Plectonema Thuret 1875 l. Plectonema Wollgi_Farlow Tilden 1910, p. 208, P1. 11, Figs. 4-5. Filaments 55-75 u broad; trichomes 43-53 u broad; cells 4-9 u long. Pl. 2, Fig. 9. In mass of filaments along shore. October. Our specimens may be forma robusta which Drouet reports as only a growth form. Microchaete Thuret 1875 1. Microchate tenera Thuret Tilden 1910, p. 203, P1. 10, Fig. 11. Filaments 15-16 u broad; trichomes 10-12 u broad; cells 8-12 u long; heterocysts 10-15 u wide, 11-19 u long. P1. 2, Fig. 1. Attached to Nymphea leaf. August. 2. Microchaete tenuissima W. and G. S. West Tilden 1910, p. 203, 21. 10, Fig. 10. Filaments 3.5—4 u broad; heterocysts 2.5—4 u broad. Cells 5—16 u in length. P1. 2, Fig. 10. 130 Family Stigonemataceae Stigonema Agardh 1824 1. §§Agpnema ocellatum (Dillwyn) Thuret Tilden 1910, p. 246, P1. 15, Figs. 15-17. Filaments 15-18 u broad; trichomes lO-14 u broad. P1. 2, Fig. 11. Collected in plankton in May. This is not a euplanktonic species and only a small secondary portion was collected. The measurements are under the typical measurements. Family Rivulariaceae Calothrix Agardh 1824 1. Calothrix gusca (Kuetzing) Bornet and Flahault Tilden 1910, p. 265, P1. 17, Figs. 10-11. Filament 13 u at base; trichomes 10-6 u at base; heterocysts 9 u broad, 6.45 u long. P1. 2, Fig. 12. Attached to Cladophora in filamentous mass along shore. October. 2. Calmhrix Juliana (Heneghini) Bornet and Flahault Tilden 1910, p. 566, P1. 16, Fig. 5. Filament 10-15 u at base; trichomes 9-12 u at base. P1. 2, Fig. 13, Attached to CladOphora in filamentous mass along shore. October. 3. Calothrix staggalis Gomont Tilden 1910, p. 265, P1. 17, Figs. 8—9. Filaments 8-1O u broad; cells 6-10 u broad; heterocysts lO-ll u broad. P1. 2, Figs. 15-16. Attached to fila- mentous algae. August. 131. Cloeotrichia Agardh 1842 1. Gloeotrichia pisum (Agardh) Thuret Tilden 1910, p. 284, P1. 19, Fig. 5. (Pivularia pisum ~Ag.) Filaments 567 u broad' heterocvcts 9 u broad 9 > ’ u ’ 1 u long. Pl. 2, 11g. 14. Attached to aquatic plant i-. on stem. Aug. Phylum CWEYSOPHYTA Class 1. XANTHOPFYCEAE Order I. UHTFHOC.CC1LES Family Ophiocytiaceae Ophiocytium Naegeli 1849 f‘ 1. hiocytium cochleare (Eichwald) A. Praun to Collins, 1909, p. 94; Pascher, A. 1925, p. 77, Fig. 60 Cells 8-10 u in diameter. Pl. 3, Figs. 2—3. Peach pool. Jay and June. 2. Qphiocytium parvulum (Party) A. Braun Smith, 920, p. 86, P1. 15, Fig. 11. Cells 8 u broad. Pl. 8, Fig. 4. Peach pool. Order HETEROTRICHALFS Family Tribonemataceae Tribonema Derbes and Solier 1858 l. Tribonema bombycinum (Agardh) Derbes and Solier Prescott, 1081, p. 47, P1. 7, Figs. 9-10 I" r-\ 0 K4 Cells 8—10.75 u broad; 2—4 diameters long. P1. 8, F1 0'52 Floating mass among reeds and grass in inlet. April and Hay 1.3.2:); 0 T 2. Tribonema minus (Wolle) dazen Prescott, 19.31, p. 47, Pl. 7, Figs. 11—12 Cells 4 u broad, Z—o liameters long. P1. 8, gig. 6. In filamentous mass in beach pool. N.y. Class 2. C"EIS9PH MC Order CWP”89“0FADALF° Sub—order P“0”9LI“I““AV Family Mallomonadaceae Mallomonas Perty 1852 1. Mallomonas caudata Iwanoff Smith, 1920, p. 69, P1. 12, Fig. 6 Cells 12-30 u broad, 40—85 u long. Pl. 5, Fig. 8. Plankton. November. Sub-order ISOCUPl IDINIAF Family Synuraceae Synura Ehrenberg 1838 l. Synura uvolla Ehrenberg Smith, 1920, p. 70, Pl. 12, Figs. 9-10 Cells 8—17 u broad, 29—35 u long. Colonies up to 350 u in diameter. P1. 8, Fig. 7. Plankton. April and May. Phylum CHLOROP1:[TA Class C ’L’V‘OPT'"C1« A 4. Order VOLVOCALES Family Volvocaceae Pandorina Eory 1824 l. Pandorina morum Bory Smith, 1920, p. 95, P1. 18, Figs. 18—17 Cells 7—8 u broad; colonies 22—87 u broad. Pl. 3, Fig. 9. Plankton. April through June. Eudorina Ehrenberg 1832 1. Eudorina e earns Ehrenberg Smith, 1920, p. 96, P1. 19, Fig. 1 Cells 14—18 u in diameter; colonies 78—l50 u in diameter. Pl. 5, F’g. 10. Plankton. April through July. Eudorina unicocca a. F. Smith v~ \ O L) Smith, 1933, p. 385, Fig. 225. Cells 18—15 u in diameter; colonies m5—120 u in diameter. Pl. 3, Fig. 11. Plankton. April through June. Pleodorina Shaw 1894 l. Pleodorina califiornica Shaw Smith, 1920, p. 97, Pl. 17, Figs. 1—8 Vegetative cells 9—11 u in diameter; reproductive cells 14—19 u in diameter. Colonies 175—2 5 u in diameter. P1. 3, Fig. 12. Plankton. July. Volvox Linnaeus 1758 13h 1. volvox aureus Ehrenberg Smith, 1920, p. 98, P1. 18, Fig. 2 Cells 5-9 u in diameter; colonies 300-509 u in dia- meter. Pl. 3, Fig. 13. Plankton. May through July. Order TETRASPORALES Family Palmellaceae Sphaerocystis Chodat 1897 l. Sphaerogystis Schroeteni Chodat Smith, 1920, p. 101, P1. 19, Figs. 3-H Cells H.3 u in diameter; colony 54-78 u in diameter. Pl. M, Fig. l. Plankton. May through July. Gloeocystis Naegeli 18M9 l. Qgpeocysgig ampla_Kuetzing Smith, 1933, p. 353, Fig. 236 B Cells 6.45 u broad, 8.6 u long. P1. h, Fig. 3. In filamentous mass along shore near inlet. June. 2. glpeocystis agg@§_(Kuetzing) Lagerheim Smith, 1920, p. 101, P1. 19, Fig. 2 Cells 6 u in diameter; colony 38-h4 u in diameter. Pl. H, Fig. 2. Plankton. May. Family Tetrasporaceae Tetraspora Link 1809 1. ggtraspora gelatinosa (Vaucher) Desvaux Prescott, 1931, p. 52. Prescott (manuscript), P1. 5, Figs. 3-4. 135 -Cells 6.45-8.6 u in diameter. Pl. M, Figs. 4-5. Attached to concrete dock. May. Order ULOTRICHALES Family Ulotrichaceae Ulothrix Kuetzing 1833 l. Ulothrix tenuissima Kuetzing Heering, 191%, p. 32, Fig. 31. Cells l5-17.2 u broad; 10-13 u long. Pl. n, Fig. 6. Scrapings from bark of submerged limb. April. 2. Ulothrix variabilis Kuetzing Prescott, 1931, p. 81. Prescott (manuscript), P1. 6, Fig. 13. Cells 22 u broad; 15-23 u long. Pl. A, Fig. 8. Attached to weeds and submerged wood. April. 3. Ulothrix zonata (Weber and Mohr) Kuetzing Prescott, 1931, p. 81, P1. 17, Fig. 22. Cells 22 u broad, 15-23 u long. 1P1. h, Fig. 8 Attached to weeds and submerged wood. April. Uronema Lagerheim 1887 1. Uronema elongatum Hodgetts Smith, 1933, p. 381, Fig. 25A. Cells 4.5 u broad, 10.75-21.5 u long. P1. n, Fig. 9. Attached to filaments of Phormidium from concrete culvert at storm sewer entrance. April. g 136 Family Microsporaceae Microspora Thuret 1850; emend. Lagerheim 1888 l. Microspora gtagnorum (Kuetzing) Lagerheim Prescott, 1931, p. 82. Prescott, (manuscript), P1. 8, Figs. 6-7. Cells 8.6 u broad, 10.75-l9 u long. Pl. h, Fig. 10. Floating masses among submerged reeds and grasses. April. 2. Jicrosppra tumidula Hazen Prescott, 1931, p. 82, P1. 18, Fig. h. Cells 6-8 u in diameter. Pl. h, Fig. 11. Filamentous mass along shore. April. Family Chaetophoraceae Stigeoclonium Kuetzing 18%3 l. Stigeoclonium lubricum (Dillwyn) Kuetzing Prescott, 1931, p. 86, Prescott, (manuscript), P1. 10, Figs. 1-2. Cells 9-11 u in diameter. P1. 4, Fig. 12. Among reeds and grasses near shore. April and May. 2. gtlgeoclonium tenue (Agardh) Kuetzing Prescott, 1931, p. 86; Hazen, 1902, p. 202, P1. 32, Figs. 1-3. Cells 6-8 u in diameter. P1. h, Fig. 13. Attached to submerged rock at storm sewer entrance. October. ChaetOphora Schrank 1813 1. Chaetophora elegans (Roth) Agardh Prescott, 1931, p. 8h, P1. 19, Figs. 1-2. 137 Cells 4 u broad; 1h-19 u long. P1. 5, Fig. 1. Attached to aquatic stem. October. Draparnaldia Bory 1808 l. Draparnaldia glomerata (Vaucher) Agardh Collins, 1909, p. 303, Fig. 89. Main axis of cells n u wide; 2 times diameter in length. Cells in fascicles 6—9 u broad. P1. 5, Fig. 2. Filamentous growth among reeds and grass in inlet. Family Coleochaetaceae Coleochaete Brébisson 18MM 1. leeochaete orbicularis Pringsheim Prescott, 1931, p. 88, P1. 22, Fig. 3. Cells 6-18 u broad, 16-32 u long. P1. 5, Fig. 3. Attached to submerged plant stems. August. 2. Coleochaete scutata Brébisson Prescott, 1931, p. 88, P1. 22, Fig. 5. Cells 2u-u5 u in diameter. 21. 5, Fig. 4. Attached to submerged plants. August. Family Trentepohliaceae Gomontia Bornet and Flahault 1888 l. Gomontia Holdenii Collins Smith, 1933, p. #17, Fig. 282. Cells 17-19 u broad, 23-28 u long. P1. 5, Fig. 5. Attached to Nymphaea stem. August. 138 Family Cladophoraceae CladOphora Kuetzing l8h3 1. Cladophora callicoma Kuetzing Collins, 1909, p. 352 Cells in primary branches 75-90 u broad, 250-360 u long; cells in secondary branches #5 u broad, l80—2OO u long. P1. 5, Fig. 6. Washings on shore near inlet. October. 2. CladOphora ggacta (Dillwyn) Kuetzing Prescott, 1931, p. 89, P1. 23, Fig. 2. Cells in primary branches 80-118 u broad,-245~272 u long; cells in secondary branches 3s-u5 u broad, 90-122 u long. Pl. 5, Figs. 7-8. Washings on shore near inlet. October. Rhizoclonium Kuetzing 18h3 l. Rhizoclonium hieroglyphicum (Agardh) Kuetzing Prescott, 1931, p. 91, P1. 25, Fig. h. Cells 25 u broad, 182-2&7 u long. P1. 6, Fig. 2. Beach pool. May. Pithophora Wittrock 1877 1. githophora Eggig,Wille Prescott, 1931, p. 91, Pl. 2h, Figs. 7-8. Filaments 60-78 u broad; akinetes 90-98 u broad, 290- 45H u long. Pl. 6, Fig. l. Intermingled with floating Cladophora near shore. October. 139 Order OEDOGONIALES Family Oedogoniaceae Oedogonium Link 1820 l. Oedogonium crispum (Hassall) Wittrock Tiffany, 1937, p. 52, P1. 22, Figs. 336-337. Vegetative cell 11-12 u broad, 43-56 u long; antheridia 10.75 u broad, 6.45 u long. P1. 6, Fig. 1. Beach pool. May. 2. Oedogonium hystric;num Transeau and Tiffany Tiffany, 1937, p. 55, P1. 30, Figs. M81-h82. Suffultory cell 21 u broad, 53 u long; oogonium 38 u broad, 40 u long; oospore 34.h u broad, 38.7 u long; antheridia 8.6 u broad, 8 u long. Pl. 7, Fig. 2. Beach pool. June. 3. Ogdogonium globosum Nordstedt Tiffany, 1937, p. 32, P1. 9, Fig. 120._ Vegetative cell 11 u broad, 81-114 u long; oogonium 38 u broad, 35 u long; oospore #1 u broad, 38 u long. Pl. 7, Fig. 3. Beach pool. June. h. Oedogonium grands Kuetzing Tiffany, 1937, p. 38, P1. 13, Fig. 172-17u Vegetative cell 38-“0 u broad; oogonium 60 u broad, 97 u long; oospore 56 u broad, 73 u long. Pl. 7, Fig. 4. Beach pool. June. \ 5. Oedogonium princeps (Hassall) Wittrock Tiffany, 1937, p. 36, P1. 11, Figs. 1u7-15o. 1&0 Vegetative cells M3 u broad; oogonium 53 u broad, 81 u long; oospore 51 u braod, 51 u long; antheridium 43 u broad, 8 u long. P1. 7, Figs. 5-6. Beach pool. June. 6. Oedogonium ppsaliense Wittrock Tiffany, 1937, p. 3A, P1. 10, Fig. 133. Vegetative cells 15 u broad; suffultory cell 23 u broad; oogonium 53 u broad, 96 u long; oospore 50 u broad, 86 u long; antheridium 15 u broad, 7 u long. P1. 7, Fig. 7. Beach pool. May. Order ULVALES Family Schizomeridaceae Schizomeris Kuetzing 1843 1. Schizomegig Leibleinii Kuetzing Prescott, 1931, p. 81, P1. 18, Figs. 1-2. Cells 15-53 u in diameter; holdfast 13 u in diameter. Pl. 6, Figs. 3—4. Attached to submerged rock at storm sewer entrance to lake. October. Order CHLOROCOCCALES Family Hydrodictyaceae Pediastrum Meyen 1829 1. Pediastrum Boryanum (Turpin) Meneghini Smith, 1920, p. 169, Pl. #5, Figs. 2-7. Diameter cells 12 u. Diameter 16—celled colony 6M u. Pl. 8, Fig. 1. Common in plankton. Spring. 2. Pediastrum duplex Meyen 1M1 Smith, 1920, p. 171, P1. M6, Figs. lM-l6. Diameter of cells 13—18 u; diameter of colony 110 u. Pl. 8, Fig. 2. Plankton. July. 3. Pediastrum duplex var. glpthratum (A. Braun) Lagerheim Smith, 1920, p. 171, P1. M7, Figs. 1-3. ‘ Diameter of cells 22 u. P1. 8, Fig.3. Plankton. July. M. Pediastrum tetres var. tetraodon (Corda) Hansgirg Smith, 1920, p. 17M, Pl. M8, Figs. 13-1M; Pl. M9, Figs. 1-2. Diameter of cells 8 u. Pl. 8, Fig. M. Scrapings from aQuatic plant stems. August. Sorastrum Kuetzing, 18M5 1. Sorgstrum gmgricanum var. undulatum G. M. Smith Smith, 19203 p. 163, P1. MM, Figs. 2-3. Cells 7-10 u broad. P1. 3, Fig. 5. Mixed in a filamen- tous mat along shore. June. Hydrodictyon Roth 1800 1. fiyggodictyon reticulgtum (Lund) Lagerheim Smith, 1920, p. 166, P1. MM, Fig. 6, Pl. M3, Fig. 1. Cells 5-M2 u broad. P1. 8, Fig. 1M. Forming heavy mats along shore. Summer. Family Coelastraceae Coelastrum Naegeli 18M9 l. Coelastrum_microporum Naegeli Smith, p. 160, Pl. A1, Figs. 12—13, Pl. A2, Fig. 11. 1M2 Diameter of cells 11 u (without sheath), 13 u (with sheath). Diameter of coenobe 56 u. P1. 8, Fig. 6. Common in plankton. May and June. Family Oocystaceae Dictyosphaerium Naegeli 18M9 1. Qictyosphaerium pulchellum Wood smith, 1920, p. 105, P1. 20, Fig. 13, P1. 21, Fig. 1. Cells M.3 u in diameter. P1. 8, Fig. 9. P1ankton.May. Oocystis Naegeli 18M} 1. Oocystis Borgei Snow Smith, 1920, p. 111, P1. 22, Fig. M. Cells 8.6 u broad, 10 u long; colony 19 u in diameter. P1. 8, Fig. 7. Mixed with filamentous algae along shore. June. 2. Oocystis glliptica W. West Smith, 1920, p. 111, P1. 22, Fig. 5. ' Cells 15 u broad, 21 u long; colony 60 u broad. P1. 8, Fig. 12. Mixed with filaments of Zygnema along shore.June. 3. Oocystis lacustris Chodat Smith, 1920, p.112, P1. 22, Figs. 8—9. Cells 10 u broad, 21 u long. P1. 8, Fig. 10. Mixed with other algae along shore. June. M. Oocystis parva W. & G. S. West Smith, 1920, p. 112, P1. 22, Fig. 6. Cells 7 u broad, 12 u long; coenobe 19 u broad, 22 u long. 1M3 Pl. 8, Fig. 8. Mixed with other algae. Beach pool. June. Gloeotaenium Hansgirg 1890 l. Gloeotaenium Lgitlesbergerianum Hansgirg Smith, 1920, p. 115, P1. 23, Figs. 8—9. Cells 23 u in diameter. P1. 8, Fig. 11. Mixed with Oscgllatoria attached to bottom. August. Kirchneriella Schmidle 1893 l. Kirchneriella obesa var. mglgg (Bernard) G. M. Smith Smith, 1920, p. 1A2, P1. 35, Fig. M. . Cells 3—5 u broad, 8—12 u long. P1. 8, Fig. 13. In filamentous mixture along shore. November. Family Scenedesmaceae Scenedesmus Meyen 1829 l. Scenedesmus armatus (Chodat) G. M. Smith Smith, 1920, p. 154, P1. 39, Figs. 7-10. Cells 5.5 u broad, 15 u long; 8-ce11ed coenobe (without epines) 15 u broad, MM u long. Spines 6 u long, P1. 9, Fig. 1. Plankton. June. 2. Scenedesmus bijuga (Turpin) Lagerheim Smith, 1920, p. 152, P1. 37, Figs. 18-20. Cells M u broad, 10-12 u long; M-celled coenobe 10-12 u broad, M3 u long. Pl. 9, Fig. 2. Mixed with Spirogyra in inlet. May. 3. Scenedesmus dimorphus (Turpin) Kuetzing Smith, 1920, p. 151, P1. 37, Figs. 15-17. lMM Cells 3 u broad, 10 u long; M-celled coenobe 10 u broad, 1M u long. Pl. 9, Fig. 3. Scrapings from aquatic plant stem. August. M. Scenedesmus obliguus (Turpin) Kuetzing Smith, 1920, p. 151, P1. 37, Figs. 12-1u. Cells M.3 u broad, 15 u long. M-celled coenobe 15 u broad, 18 u long. Pl. 9, Fig. M. Scrapings from aquatic plant stem. August. 5. Scenedesmus quadricauda (Turpin) Brebisson Smith, 1920, p. 158, P1. MO, Figs. 9-11. Cells M.3 u broad, 15 u long. M~celled coenobe without spines, 1M u broad, 19.3 u long; spines 8-10 u long. Pl. 9 Fig. 5. Scrapings from aquatic plant stem. August. 6. Scenedesmus guadricauda var. ouadrisp;pg_(0hodat) G. M. Smith. Smith, 1920, p. 158, P1. M0, Figs. 15-16. Cells 6 u broad, 17 u long. M-celled coenobe without spines, 17 u braod, 25.8 u long; spines 5-6 u long. Pl. 9, Fig. 6. Mixed with filamentous algae along shore. June. Crucigenia Morren.1830 1. Crucigenia irregularis Wills Smith, 1920, p. 1M3, P1. 36, Figs. M-5. Cells M.3-5 u broad, 8.6 u long. M-celled coenobia. 8 u broad, 26 u long. Pl. 9, Figs. 7-8. Scrapings from aquatic plant stems. August. 1M5 Family Botryococcaceae Botryococcus Kuetzing 18M9 l. Bgtryococcus Brappii Kuetzing Smith, 1920, p. 8M, P1. 15, Fig. 5. Cells 5 u broad, 10.5 u long. Colony 3M u in diameter. P1. 3, Fig. 1. Beach pool. May. Order SIPHONALES Family Vaucheriaceae Vaucheria De Candolle 1803 l. Vaucheria geminata var. racemosa (Vaucher) walz. Prescott, 1931, p. 92, P1. 26, Fig. 3. Filament 81-99 u broad; stalk of reporductive organs: M3 u broad at base; antheridia 28 u wide; oogonia 75 u broad, 86 u long. Pl. 6, Fig. 5. Beach pool. May. 2. Vaucheria sessil;§.(Vaucher) De Candolle Prescott, 1931, p. 93, P1. 27, Fig. 5. Filament M3 u broad; antheridia 32 u broad; oogonia 6M-68 u broad, 77-80 u long. P1. 6, Figs. 6-7. Order ZYGNEMATALES Family Zygnemataceae iougeotia Agardh 182M 1. Mouggptia scalar;§_hassall Prescott, 1931, p. 106; Borge and Pascher, 1913, p. M1, Fig. 66. Filament 31 u broad; zygospore 3M u broad, M5 u long. P1. 11, Fig. l. Filamentous growth along shore. June. o . u . e c o o v a a o - - . \ \ —. - . . . O . O n . - \ ! ~ 0 ~ . 1M6 Spirogyra Link 1820 l. Spirogyra crassa Kuetzing Prescott, 1931, p. 107; Borge and Pascher, 1913, p. 30, Fig. M2. Filament 127 u wide; zygospore 11M u in diameter. P1. 11, Fig. 2. Filamentous growth in shallow water near boat dock. June. 2. Spirogyra decimina (Mueller) Kuetzing Prescott, 1931, p.6107, P1. 30, Fig. 7. Filament 32-38 u broad; zygospore 30-35 u broad, 53- 60 u long. P1. 11, Fig. 3. Filamentous growth along shore in inlet. May. 3. Spirogyra lutetgana Petit Collins, F. C., 1909, p. 3M; Borge, O. and Pascher, 1913, p. 25, Fig. 30. Filament 39-M5 u broad; zygospore 32-M3 u broad, 55—75 u long. P1. 11, Fig. M. Beach pool. May. O M. Spirogyra mirabilis (Hassall) Kuetzing Prescott, 1931, p. 109; Borge and Pascher, 1913, p. 21, Fig. 17. Filament 27 u broad; zygospore 30 u broad, 53-55 u long. P1. 11, Fig. 6. Beach pool. July. 5. Spirogyra porticalis (Mueller) Cleve Prescott, 1931, p. 109; Smith, G. M., 1920, p. 185, P1. 51, Fig. 3. 1117 Filament M1 u broad; zygoSpore MO u broad, 73-86 u long. P1. 11, Fig. 7. 'Plankton tow. June. Smith lists this species as planktonic. 6. Spirogyra Spreeiana Rabenhorst Prescott, 1931, p. 110; Borge and Pascher, 1913, p. 17, Fig. 5. Filament 17-18 u broad; zygospore 25-32 u broad, 86- 116 u long. P1. 11, Fig. 5. Beach pool. June. 7. Spirogyra Sp. Filament 28-32 u broad; zygospore MO-M9 u broad, 75- 117 u long. P1. 12, Figs. l-M. Beach pool. May. This specimen appears to be a new species. Proper publication will ensue if thorough investigation shows it to be thus. Family Desmidiaceae Closterium Nitzsch 1817 1. Closterium acerosum (Shrank) Ehrenberg Smith, 1925, p. 10, P1. 53, Fig. 1. Cells 320-336 u long, 21. 5 u broad at girdle. Pl. 9, Fig. 10. Plankton. July. 2. Closterium acegpsum var. elongatum Brébisson Irenee-Marie, 1938, p. 72, Pl. 6, Fig. 6. Cells 563 u long, 28 u broad at girdle. P1. 9, Fig. 11. Mixed in filamentous algae among reeds at inlet.Hay. 3. Closterium gracile var. elongatum W. & G. S. West Smith, 192M, p. 11, P1. 53, Fig. 2. Cells 608 u long; 20 u broad at girdle; M.3 u broad at a c . . . D I ' x u . .- \ ’ ‘ n w x O n u ' O \ \ O o ‘ . 1M8 poles. Pl. 9, Fig. 9. Mixed with filamentous algae along shore. May. M. Closterium lunula (Mueller) Ralfs Irenee-Marie, 1938, p. 73, P1. 6, Fig. 2-5. Cells MOO-M09 u long; 56-6M u broad at girdle; 6.M5 at poles. Pl. 9, Fig. 2. Plankton tow. May. 5. glggterium moniliferum (Bory) Ehrenberg ' Smith, 192%, p. 9, P1. 52, Fig. 10. Cells 225 u long; 35 u broad at girdle; M.3 u broad at poles. Pl. 9, Fig. 13, Plankton. May. 6. gigggerium parvulum Naegeli Irenee-Marie 1938, p. 68, Pl. M, Figs. M-6. Cells 96 u long; 11.5 u at girdle; 3 u broad at poles. P1. 9, Fig. 1M. Mixed with filamentous material at storm sewer entrance. October. This form is close to Closterium venus. The curvative appears more pronounced than Closterium parvulum, but the measurements place it here. Pleurotaenium Naegeli 18M9 l. Pleurotaenium trabecula (Ehrenberg) Naegeli Smith, 192M, p. 1M, Irenee-Marie, 1938, p. 9M, P1. 10, Figs. 5-6. Cells 56M u long; 37 u at base; 23.6 u at poles. P1. 9, Fig. 15. Beach pool. May. Cosmarium Corda 183M 1. Cosmarium angulosum Brebisson 4‘ 1M9 Irenee—Marie, 1938, p. 177, P1. 2M, Fig. 5. Cells 1M u wide; 17.2 u long. Pl. 9, Fig. 17. Beach pool. May. 2. Cosmarium angglosum var. conc$pnum (Rabenhorst) W. & G. S. West. Gronblad, 192M, p. 7, Pl. 2, Figs. 31-35. Cells 12.9 u wide; 18 u long. M u wide at isthmus. Pl. 9, Fig. 16. Attached to aquatic plant stem. August. 3. Cosmarium Botrytis (Bory) Meneghini Smith, 192M, p. 33, P1. 57, Fig. 22 Cells 56 u wide; 69 u long; 15 u at isthmus. Pl. 9, Fig. 18. Beach pool. June. M. Cosmarium connatum Brébisson Irenee-Harie, 1938, p. 173, P1. 22, Figs. 8-9. Cells M3 u broad; 70 u long; 39 u at isthmus. P1. 9, Fig. 19. Mixed with filamentous algae along shore. Oct. 5. Cosmarium geniform§_(Ra1fs) Archer Smith, 192M, p. 33, P1. 57, Fig. 23. Cells M7 u broad; M7 u long; 16 u broad at isthmus. Pl. 9, Fig. 21. Scrapings from aquatic plant stem. Aug. 6. Cosmarium sub-reniforme Nordstedt Irenee-Marie, 1938, p. 19M, P1. 31, Fig. 17. Cells 35 u broad; 37 u long; 10 u broad at isthmus. P1. 9, Fig. 21. Mixed with Zygnema filaments floating among lily pads (Nymphaea). August.- (o 150 7. Cosmarium Turpini Brébisson Irenee-Marie, 1938, p. 199, P1. 6, Fig. 1. Cells 58 u broad; 71 u long, 17 u broad at isthmus. Pl. 9, Fig. 22. Beach pool. May. - Staurastrum Meyen 1892 1. Staurastrum alternans Brébisson Smith, 1924, p. 70, P1. 68, Fig. M. Cells 30 u broad; 3M u long; 10.75 u broad at isthmus. P1. 10, Fig. 5. Among filamentous algae in reeds in inlet. May. 2. Staurastrum chaetoceras (Schroeder) G. M. Smith Smith, 192M, p. 99, P1. 76, Figs. 21—2M; P1. 77, Fig. 1. Breadth with processes 65 u, without processes 21 u; length with processes 65 u, 25 u without processes; breadth at isthmus 7 u. P1. 10, Fig. 1. Plankton, November. 3. Staurastrum gracile Ralfs Irenee-Marie, 1938, p. 313, P1. M8, Fig. M. ,Cells 60 u long with processes, 28 u long without processes; breadth with processes 65 u, breadth without processes 13 u; breadth 8.6 u at isthmus. P1. 10, Fig. 3. Plankton. July. M. Staurastrum longiradiatum W. & G. S. West Smith, 1925, p. 90, Pl. 7M, Figs. 5-11. Cells M6-96 u long with processes, M3 u long without processes; 86 u broad with processes, 20—28 u broad without 151 processes; 10.75 u broad at isthmus. P1. 10, Fig. 2. Plankton. July. 5. Staurastrum pgradoxum Meyen Smith, 192M, p. 85, P1. 72, Figs. 15—22; P1. 73, Figs. 1-2. ' Cells 37-65 u long with processes, 25-35 u long without processes; breadth with processes 57-88 (83) u, without processes 18-25 (22) u; breadth at isthmus 7.5-11 u. P1. 10, Fig. M. Plankton. July. Phylum PYRRHOPHYTA Class DINOPHYCEAE Order PERIDINIALES Family Peridiniaceae Peridinium Ehrenberg 1832 l. Peridin;gm cingtum (Mueller) Ehrenberg Prescott, (manuscrOpt), P1. 91, Figs. l-M. Plankton. Ma rch . Family Ceratiaceae Ceratium Schrank 1793 l. Ceratium hlgundinella (O. F. Mueller) Du Jardin Smith, G. M., 1933, p. 605, Fig. M28. P1. 10., Fig. 6. Common in summer and early fall plankton. 152 Phylum EUGLENOPHTXA Family Euglenaceae Englena Ehrenberg 1838 1. Englena acus Ehrenberg Prescott, 1931, p. 1M2; Walton, 1915, p. 371, P1. 1M, Fig. 8. Cells 193 u long, 18 u broad. P1. 10, Fig. 7. Storm Sewer. June. 2. Englena proxima Dangeard Prescott, 1931, p. 1M3; Walton, 1915, p. 367, P1. 13, Fig. M. Cells 97 u long, 21.5 u broad. P1. 10, Fig. 8. Plank- ton. May. Fig. l. 11. .12. 13. 1M. 15. 16. 17. 18. 19. 20. 21. 22. 153 Plate 1. Chroococcus dispersus (v. Keissler) Lemmermann (x M301 Q. limneticus var. carneus (Chodat) Lemmermann (x M30). 9. minutus (Kuetzing) Naegeli (x M30). Ferismopedia tenuissima Lemmermann (x M30). Microcystis aeruginosa Kuetzing (x 215, x 100). g. aeruginosa var. mglgg G. H. Smith (x M30). Ashanothece stagnalig (Sprengel) A. Braun (x M30). Coelosphaerium Naegelianum Unger (x M30). Soirulina major Kuetzing (x M30). Arthrospira Jenneri (Kuetzing) Stizenberger (x M30). Oscillatoria Agardhii Gomont (x M30). 9. amphibia Agardh (x M30). g. Chlorine Kuetzing (x M30). 9. formosa Bory (x M30). g. limnetica Lemmermann (x M30). ,9. limosa Agardh (x M30). 9. rubescens De Candolle (x M30). 0. sancta Kuetzing (x M30). 9. princeps Vaucher (x M30). IO . tenuis Agardh (x M30). Phormidium Retzii (Agardh) Gomont (x M30). vagbya aerugineo-caerula (Kuetzing) Gomont (x M30). L. Aestuarii Gomont (x M30). L. Biggei s. M. Smith (x M30). Fig. 26. 27. 28. 29. 30. 31. 32. 33- 3M. 15M Plate I.-cont. L. Hieronymusii Lemmermann (x M30). IL“ . penicillata Kuetzing (x 860). A. epiphytica Hieronymus (attached to Toly- pothrix) (x 950). Microcoleus paludosus (Kuetzing) Gomont (x 375). Anabaena Gircinalis var. macrospora (Wittrock) De Toni (x M30). A. cylindrica Lemmermann (x M30). A, limnetica G. M. Smith (x M30). A. oscillarioides Bory (x M30). A. spiroides var. crassa Lemmermann (x 215). Plate 1 a a... *- 7 81%&: 9 .. 155 Plate II. Fig. 1. Anabaena Lemmermannii P. Richter (x 215).- 2. Nostoc micrOSCOpicum Carmichael (x M30). 3. Aphanizomenon flos-aquae (Linnaeus) Ralfs (x 187.5). M. Nostoc paludosum Kuetxing (x M30). 5. Aphanizomenon flos-aquae (Linnaeus) Ralfs (x M30). 6. Cylindrosoermum stagnale (Kuetzing) Bornet and Flahault (x M30). 7. Tolypothrix lanata (Desvaux Wartmann (x 215). 8. Microchaete tenera Thuret (x 215). 9. Plectonemw Wollei Farlow (x 215). 10. Microchaete tenuissima W. & G. S. West (x M30). 11. Stigpnema ocellatum (Dillwyn) Thuret (x 215). 12. Calothrix fusca (Kuetzingl Bornet and Flahault (x M30). 13. Q. Juliana (Meneghini) Bornet and Flahault (x M30). 1M. Gloeotrighgg piggmi(Agardh) huret (x 215). 15-16. Calothrix stagnalis Gomont (x M30, x 50). Plate 2 we 1%. 4mm em III _ “ ‘ ' $2: ’ § 5:: ’s" 8 Fig. 1. 2-3. 10. ll. 13. 156 Plate III. Bptryococcus Braunii Kuetzing (x M30). Ophiocytium cochleare (Eichwald) A. Braun (x M30). ' Q. parvulum (Perty) A. Braun (x M30). Tribonema bombycinum (Agardh) Derbes and Seller (x M30). ,1. mlpp§,(Wolle) Hazen (x M30). Synura uvella Ehrenberg (x M30). Mallomonag caudata Iwanoff (Redrawn from G. M. Smith 1920) (x 250). Pandorina morum Bory (x M30). Eudorina elegans Ehrenberg (x M30). E. unicocca G. M. Smith (x M30). Pleodorina californica Shaw (x 215). Volvox aureus Ehrenberg (x 100) (Modified after G. M. Smith 1920). Plate 3 ‘5' ‘ iv. '69 .0; 1'8".“ 0" w.“ I: 1 « unit. :5“. ‘1é0“‘.q ‘53. "\ "‘ 1'." . 11-5. \0 10. ll. 12. 13. Plate IV. Sphaerocystis Schroeteri Chodat (x M30). Gloeocystis gigas (Kuetzing) Lagerheim (x M30). g. ggp;g_Kuetzing (x M30). Tetraspora gelatinosa (Vaucher) Desvaux (portion of colony x 215) (Habit of colony x 10). Ulothrix tenuissima Kuetzing (x M30). g. variabilis Kuetzing (x M30). g, zonata (Weber and Mohr) Kuetzing (x M30). Uronema elongatum Hodgetts (x M30). Microspora stagnorum (Kuetzing) Lagerheim (x M30). M, tumidula Hazen (x M30). Stigeoclonium lubricum (Dillwyn) Kuetzing (x 215). §3 tgpgg (Agardh) Kuetzing (x 215). Plate h Fig. l. 158 Plate V. Chaetoohora elegang (Roth) Agardh (x M30). Q;aparnaldia_glgmerata (Vaucher) Agardh (x 215). Coleochaete orbicularis Pringsheim (x 215). C. Scutata Brebisson (x 215). Gomontia Holdenii (x 215). Cladophora callicoma Kuetzing (x 215). Q. fracta (Dillwyn) Kuetzing (x 50, x 100). Plate 5 ‘ ,7 ' ' “ ”fir ._. . s l . ”‘2, d1 - ‘9- J.- 33:3 ” O a a ‘f t n 'h }- t' M" o i a . 1‘ fi .321‘ ‘- l p - r; ;, ~ F «.1 any)“ (8” .fi-fi‘ :: V‘ if“ \/ .. ..L 159 Plate VI Pithophora varia Wills (x 50). Rhizoclonium hieroglyphicum (Agardh) Kuetzing (x 100). Schizomeris Leibleinii Kuetzing (x M30, x 215). Vaucheria geminata var. racemosa (Vaucher) Walz (x 215). 1. sessilis (Vaucher) De Candolle (x 215.) Plate 6 3.8. ....w 9% segues. ...“. newsm. EW .9“ . Shawna. 160 Plate VII. Fig. l. Ogdogonium crispum (Hassall) Wittrock (x M30). 2. O. hystricinum Transeau and Tiffany (x M30). 3. Q. globosum Nordstedt (x M30). M. g. grands Kuetzing (x 215). 5-6. Q, pginceps (Hassall) Wittrock (oogonial filament x M30) (antheridial filament x M30). 7. Q. ppsaliense Wittrock (x 215). Plate 7 Fig. 10. 11. 12. 13. 1M. 161 Plate VIII. Pediastrum Boryanum (Turpin( Meneghini (x M30). P, duplex Mayen (x M30). P, duplex var. clathratum (A. Braun) Lagerheim (x M30). P; tetras var. tetraodon (Corda) Hansgrig (x M30). Sorastrum amerieanum var. undulatum G. M. Smith (I: M30). Coelastrum microporum Naegeli (x M30). Oocystis Borgei Snow (x M30). 9, pg§1g_w. & G. S. West (x M30). Dictyosphaerium pulchellum Wbod (x M30). Oocystis lacustris Chodat (x M30). Gloeotaenium Loitlesbergerianum Hansgirg (x M30). Oocysti§_elliptica W. West (x M30). Kirchneriella obesa var. mg1g§_(Bernard) G. M. Smith (x M30). Hydrodicyton reticulatum (Linnaeus) Lagerheim (x 100). "-11 0Q 162 Plate IX. 1. Scenedesmus armatus (Chodat) G. M. Smith (x M30). 2. S: bijuga (Turpin) Lagerheim (x M30). 3. S: dimorphus (Turpin) Kuetzing (x M30). M. S: obliquus (Turpin) Kuetzing (x M30). 5. S: quadricauda (Turpin) Brebisson (x M30). 6. S;_ quadricauda var. quadrispina (Chodat) G. M. Smith (xM30). 7-8. Crucigenia irregularis Wills (x M30). 9. Closterium gracile var. elongatum W. & G. S. West (x 100). 10. g, acerosum (Schrank) Ehrenberg (x 15M). 11. g, acerosum var. elongatum Brebisson (x 100). 12. g, lunula (Mueller) Ralfs (x 100). 13. g, moniliferum (Bory) Ehrenberg (x 215). 1M. Q, parvulum Naegeli (x M30). l5. Elgurgtagnium trabecula (Ehrenberg) Naegeli (semi-cell) (x 215). 16. Cgsmapium angulosum var. concinnum (Rabenhorst) (x M30). 17. Q, angulosum Brebisson (x M30). 18. Q. Botrytis (Bory) Meneghini (x 215). 19. Q. connatum Brebisson (x 215). 20. Q. subreniforme Nordstsdt (x M30). 21. g. reniforme (Ralfs) Archer (x M30). 22. Q Turpini Brebisson (x 215). Plate 9 {884.58%ng .. $1, ’11 072 163 Plate X. Staurastrum chaetoceras (Schroeder) Smith (3: M30,) . S. lengiradiatum W. 8 G. S. West (x M30). 8. gracile Ralfs (x M30). 8. paradoxum Keyen (x M30). g . alternans Brebisson (x M30). Ceratium hirundinella (O. F. Mueller) Schrank (x M30). Englena acus Ehrenberg (x M30). g. proxima Dangeard (x M30). Plate 10 “.'o. Q " v u" 0"” 3::‘l'llu- I"! U ' 03!; ()4 ill .— «n.. Fig. 16M Plate XI. Morugeotia scalaris Hassall (x 215). Spirogyra crassa Kuetzing (x 100). S. decimina (Mueller) Kuetzing (x 215). S. lutetiana Petit (x 215). S. Spreeiana Rabenhorst (x 100). S. mirabilis (Hassall) Kuetzing (x 215). S. portioalis (Mueller) Cleve (x M30). Flats ll Fig. 1-M Spirogyra Sp. Plate XII. (x 215). 165 flats 12 166 IX. BIBLIOGRAPHY I 1. 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