EPA-600/3-78-033
March 1978 Ecological Research Series
EFFECTS OF DIVERSION
AND ALUM APPLICATION
ON TWO EUTROPHIC LAKES
Environmental Research Laboratory
Office of Research and Development
U.S. Environmental Protection Agency
Corvallis, Oregon 97330
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RESEARCH REPORTING SERIES
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EPA-600/3-78-033
March 1978
EFFECTS OF DIVERSION AND ALUM APPLICATION
ON TWO EUTROPHIC LAKES
by
G. Dennis Cooke1
Robert T. Heath1
Robert H. Kennedy1
Murray R. McComas2
1 Department of Biological Sciences
2Department of Geology
Kent State University
Kent, Ohio 44242
R 801936
Project Officer
Kenneth W. Malueg
Special Studies Branch
Corvallis Environmental Research Laboratory
Corvallis, Oregon 97330
CORVALLIS ENVIRONMENTAL RESEARCH LABORATORY
OFFICE OF RESEARCH AND DEVELOPMENT
U.S. ENVIRONMENTAL PROTECTION AGENCY
CORVALLIS, OREGON 97330
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DISCLAIMER
This report has been reviewed by the Corvallis Environmental Research
Laboratory, U.S. Environmental Protection Agency, and approved for publica-
tion. Approval does not signify that the contents necessarily reflect the
views and policies oE the U.S. Environmental Protection Agency, nor does
mention of trade names or commercial products constitute endorsement or
recommendation for use.
11
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FOREWORD
Effective regulatory and enforcement actions by the Environmental Pro-
tection Agency would be virtually impossible without sound scientific data on
pollutants and their impact on environmental stability and human health
Responsibility for building this data base has been assigned r_> EPA's Office
of Research and Development and its 15 major field installation, one of which
is the Corvallis Environmental Research Laboratory (CERL), in Oregon.
The primary mission of the Corvallis Laboratory is research on tn<->
effects of environmental pollutants on terrestrial, freshwater, and marine
ecosystems; the behavior, effects and control of pollutants in lake systems;
and the development of predictive models on the movement of pollutants in tr^
biosphere.
This report provides a valuable contribution to knowledge of 1 )«<-
restoration and eutrophication control espec la I \ in areas of diversion am-
in-lake treatment.
A, P. B.utsrh
Pir fK'U'r
O.' i va i ; i s En /1 r onmer: t a <
Resear fh Labor.it ory
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ABSTRACT
Two questions were asked: <\\ Will diversion of septic tank drainage
from East (ETL) and West (WTL) Twin Lakes, two shallow ( <5M), morphornetri-
cally similar, dimictic lakes in Nor tho^'-T n Ohio, bring about reduced
symptoms of eutrophication and (/) will a maximum hypolimnetic dose of
aluminum sulfate to 'WTL, def inex<-p.--tr. ().()'> mg Al/1, reduce internal
phosphorus (P) loading and further n>.prov< ' n<- l.nke?
w>>i
A return to normal fecal coliform
occurred after diversion. While P in <-t
to an "acceptable" level (VolJenwpid^s ,
important P source. P in the lakp<- wis
tion, measured as algal standing <-\<^i
(1972), but P and biomass levels r<>rna'np
eutrophic lakes. Had diversion no* o-
closed to recreation due to ^XCP^S i v.-
very eutrophic.
The P content of the lakes varied
pre-thermal stratification low, followed i«y <\
100% of which was due to net internal p ioadi
this loading was hypolimnetic in origin, H'J
were added to the hypolimnion of WTl. in July
control. Alum was earlier shown t<- ho >
sediment P release for up to two yeai e m col
jutu columns. The dose as defined «>.<- r-.h-
to certain littoral invertebrates.
in the study streams and lakes
was reduced, income did not fall
. '^roundwater was found to be an
--d, and symptoms of eutrophica-
> i educed just after diversion
i within i^nges expected of moderately
c.irifd, Mie lakes would probably be
oli!->rm levels and be classified as
from a late winter high to a
increase over the summer, up to
i. Based on the hypothesis that
r> M5 (16,919 gals) of alum
/r , leaving ETL as a downstream
"Mve in retarding anaerobic
i ak>>, and up to 104 dciys in _in
) t o- OP non-toxic to fish and
Hypolimnetic P concentration
internal P loading, while reduced,
suggesting the littoral as an
Epi limnetic P was also lowers i, _;r
reduction in symptoms, but WTL remiint'd
or excessive concentrations of: 1 1 'Un .
obsei' vecl.
v,,i« tireatly lowered, but net
- t .1 significant rate, strongly
.. i < :phir ,U,ite Index indice.ted some
'it < <.ph i ' iri 1976. No adverse; effects
ui , suliato or hydrogen ion were
The treatment may continue to !»-> p{f<-" n\,o, Imt could be overcome by
contlnue'd excessive loading resulting ti -in p>'<>r latul management.
IV
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It is suggested that hypolimnetic alum applications may be more effective
in large lakes where seiches and vertical entrainment of hypolimnetic P are
more significant. The cost for these lakes could be excessive.
Details for determining and applying an alum dose are given.
This report was submitted m fulfillment of Project Number 16010 HCS,
Contract Number R 801936, by Kent State University, under the (partial)
sponsorship of the U.S. Environmental Protection Agency. This report covers a
research period from November 197! to January 1976, and work was completed :.n
June 1977.
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CONTENTS
Disclaimer i i
Forewor d « ii i
Abstract - iv
Figures - ....... . . . i x
Tables ..«.,..,......,.. ........ xi
Acknowledgment. ...,.., xiii
I. Intr oduet ion 1
2. Conclus ions .......... 3
3. Recommendations 4
4 . Wat«r shed Character ist ics , ,,,.., 5
Gee, Sog; . 5
LV, it s r a 1 Dev <-> 1 opraent .................... 8
Limnology 8
"~i. MateL Lai.; and Methods 13
Hydr ology . . , , 13
L ] mno 1 oq\- 18
A ; ;,rn: ~,\i^ Scl ' dt e Appl ioa rion , 19
t. Wc-HU'i---, ,.,,, ., 22
Intr .-duct ; .ri .,.,,.., , , , 22
K\ id*-ru:e ot P(.< >gpho-us Lin i tat ion . , 22
W-iter and Phosphorus Badgers , 29
S^;,'t i ',. Tank 1.1 vet sion ................ 29
Ffiet.'t. M! L'lversion on Watet and Phosphorus Budgets ........ 29
Wat PI budqe t , , 29
Phosphor u.s budget , 33
Vol 1 eiweid^r phosphorus Loading mode. 1 , 41
Effects of Divei :>ion and Treatment, or. PhospMo; us ............... 4)
rnurif'd lat P effects of aluminum sulfat e 11 eatment ........... 4J
Eft ec.ts 01 phosphorus; content ot the SaKe?' ........ , 44
i it <-M na i phosphor ur> i oa 1i ng ..... 57
Kt ;-'-;! ,i Cor ^uo'tanc'r, pH, Alkdlinity, ind Aiurcinum ., ....... 61
'" <:>.";. I ',-.' : )t; a'ld Tiea'.ment or ''. . . . -;-.\ Indi>..,at i .,.,. (, f:
C< > i i tor ",; L.U':; -; »d . , ..,.,.. , ..,,....,.. b2
C<- i I Volume, .'*, lot opn/11, Phytopld'm t,.T', .--,: -. .;'
Ti ..jrsspar enc> ,.....,..,.....,. 6*
Oxy ^en L".»!. i <:11r. 70
Mac.-: ophyt.es , ....... 70
Troph ;.- State Index 70
7. Di.s<"ir,=;ion 73
References 76
VII
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Appendix 81
Introduction 81
Dose Determination Experiment 81
Phosphorus Removal Efficiency 83
In Situ Column Experiment 85
Aluminum Toxicity Exper iment 86
Dollar Lake Treatment , 89
Dose Determination for West Twin Lake Treatment , 89
Alum Application 95
Equipment for Alum Application 97
Alum Application Procedures 100
Cost of West Twin Alum Application LOO
Vlll
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FIGURES
Number Page
1 Glacial stratigraphy of the Twin Lakes Watershed 6
2 Surficial materials in the Twin Lakes Watershed 7
3 Depth contours of the Twin Lakes 10
4 Location of streams enter ing Twin Lakes and Dollar Lake 14
5 Relation between mean epilimnetic chlorophyll a_ and
spring phosphorus concentration at Twin Lakes 24
6 Relationship between algal cell size and alkaline
phosphatase activity 27
7 Alkaline phosphatase activity, specific activity and cell
volume in East Twin Lake, 1972 28
8 Percent septic tank diversion during 1972-1974 30
9 Location of piezometers in and around experimental
leach field , 35
10 Total phosphorus concentration above, in, and below
experimental leach field after diversion 36
11 Phosphorus concentration, water discharge and cumulative
sewer tie-in, stream 2S 37
12 Phosphorus discharged by stream 2S to West Twin
after diversion 38
13 Positions of East and West Twin Lakes on Vollenweider
(1976) loading diagram, 1972-1976 42
14 Alkalinity and pH of West Twin before and after hypolimnetic
aluminum sulfate application 45
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Number Page
15 Soluble reactive and filterable total phosjphorus of
West Twin before and after hypolimnetic aluminum sulfate
application . ., ............................................ 47
16 Total phosphorus and dissolved oxygen of West Twin
before and after hypolimnetic aluminum sulfate application 48
17 Phosphorus content of West Twin Lake, 1972-1972 ............ 49
18 Phosphorus content of East Twin Lake, 1972-1976 ............. 50
19 Mean seasonal total phosphorus concentration in East
and West Twin Lakes, 1971-1976 ......... ................... 52
20 Mean filterable total phosphorus concentration in the
Twin Lakes, 1973-1976 .................. ................... 53
21 Mean soluble reactive phosphorus concentration in East
and West Twin Lakes, 1971-1976 ......... ..... .............. 54
22 Changes in summer surface cell volume of the Twin
Lakes 1971-1976 ........................................... 64
23 Changes in summer surface chlorophyll a^ of the Twin
Lakes, 1971-1976 ...................... ... ................. 66
24 Changes in summer surface seston of the Twin
Lakes 1971-1976 .......................... ................. 67
25 Changes in summer transparency of the Twin
Lakes, 1971-1976 ......................... ................. 68
A-l Relationships of aluminum dose, residual dissolved
aluminum, and lake water alkalinity ...... ................. 82
A-2 Generalized model of the relation of maximum aluminum
sulfate dose and lake water alkalinity ... ................. 84
A-3 Relationship of Baume (60 F) and percent A-U0 ............ 93
A-4 Temperature correction factors for 32-36 Be' liquors ...... 94
A-5 Curve to determine pounds of alum/gallon based on
adjusted Baume1 ......................... ................. 96
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TABLES
Number Page
1 Land use in Twin Lakes area, 1850 to 1880 8
2 Limnological features of the Twin Lakes watershed 9
3 Seasonal and annual volume-weighted averages (-1971)
of selected chemical and physical features of the Twin
Lakes 'u<;,. i , , 11
4 SO;K .':*, receiving water and measuring techniques of
suiface streams in Twin Lakes Watershed 15
5 Rate of annual ^. iridwater flow into the 'IVin Lakes,
computed from f ivt- t '-cheques . 17
6 Inorganic N/Soluhle reactive *v:qht rat ins 23
7 Algal assay procedure: East Twin «,' , , , . , . 25
8 Sources of annual water (M~' x 10'; and pho:;p; , r :-;
(Kg) income-outgo for West Twin Lake
3 i
9 Sources of annual water (M x 10 ) and phosphorus
(Kg) income-outgo for East Twin LaK^ .,...,
10 Mean annual phosphorus concentration in water sources ..... 33
11 Water - phosphorus budgets of West Twin Lake 1972-1976 .... 39
12 Water - phosphorus budgets of East Twin Lake 1972-1976 .... 40
13 Pre- and post treatment aluminum concentrations
(lag Al/1) in West Twin Lake after 5 M aluminum sulfate
application .............. . .................... ........... 43
14 Sulfate (mg SO /I) in East and West Twin before and
after hypolimnetic alum application ...,....., ....... ... 46
15 Rate of increase in phosphorus content; spring low to
summer high ................................... . ......... 51
XI
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Number^ page
16 Observed and predicted (Dillon and K^glei . 97 n.-.oti
coefficients in the Twin Lak""; . 60
21 Fecal coliform colony forming units (#/i.iOn=ii in urban
stream (25) 63
22 Mean percent phyla and species compost t-i->n '>f August
surface (0.1 M) samples - 69
23 Oxygen deficits of East and West Twin ; < f 70
24 Trophic State Index 71
A-l Percent mortality of Pin>ep_hales promeLaf, -if if,- r-.no week ... 87
A-2 Benthic T-.eLMj-.vert^orates ut '-r ">;' ' ' 'if-itment 88
A-3 Diversity index values on sampling nit"", "f each group .... 88
A-4 Total phosphorus concentration in water- ff'tn -teated and
untreated anaerobic Dollar Lake S'-- r, 89
A-5 Jar test results-dissolved aluminum .'oncentrat ion (mg Al/1) 91
A-6 Gallons of aluminum sulfate applied to w."U IVir Lake 98
A-7 Cost for the aluminum sulfate treatment «f Wf-st Twin
Lake , - . . 101
K\ I
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The :p- ; [ t * Ken* " \- . r - -dr t iC'iJar 1- the Depart -
ments r-t H> ' ;. , ,..,,-( (;p, , ,r_. ,m, t >^ Vn'i-t for t'rba" Regionalism
nnd Env:ronme - , > , >* ' !y ic-k': *«. K^iq-^d, Dr:~. Eugene P.
Wenninger, 'hat .(. " ' . - . ' ' A :'e;-, J :-", ~u,<.i Mrs. (."a'' ; I'oncar were
par t L- j 1 ar J . .:-pD--'< , '!. t~i''-w::-; ^raciuaf3 -.tudents were
act ive in r^-u'Tf'^ . . . . '> ; < ' - r , M, ^;> -n fReiser) ,
0, Ft a'.',",- ^ ;..-." ' " - - , a. ', !?. T. T.ori i ,
R. T ' , ^ .,->>: , . .- , . . . , r ,-.>.. i% , : -, .
Tne.i WIT" -.'X.'r ;'->' , i i .,:,> . - 4 -- -.pe^Uij
mention ">t J. a^okwi ! arm 1), Waiier , w.^io v"it t : -nif T i.--h of the data
organization should be made. Special thanks is extended to E. Rernhardt, N.
Brown, R. R'szzi, F, Daqher , and M. Eiben (Kaiser i for their -:<-'- ;(>r]t work as
laboratory *eo', r>ic: lan--1. Tti*" r H ^ T' ;; < <= f'i i i'. - -k- >«. ! ^H T- ' " * i 'i!,;l
typiriu 11 i (li-j.-r lal i"" ' "-*" u.: ' .' ;<.")'' ''">!!': ."rvn a i .."ompan.*
pro'-idf.i -.o -i.,,." '/-.-! t - - !'ii " s- - i- - ' H. Zu^-r, '.f Allied
ChH-inc-1 - "v i >-^' . - -- a.-v-;- - -,-»-. ' r- t^search
wc.ij;i] ru t .:,' - r- p. p. ' : i~ v i ' '',( i .,,.1 - . >p'- r i* ion -;f the
Twin LaK>-' ^s^o.; i. i t ic >ri arvi the - :;.-'- '-.,',!, [.dk^-a Waternned.
x 111
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SECTION 1
INTRODUCTION
Eutrophication is the process of enrichment of lakes with plant nutrients
and particulate matter which leads to increased biological production and
decreased lake volume. This is a natural process which occurs at varying
rates, depending upon factors such as soil type and ratio of drainage area to
lake surface area, and upon lake properties such as mean depth and flushing
rate. Where activities on the land are intense, the rate may be greatly
accelerated by erosion or sewage income, leading to what has been termed
"cultural" eutrophication. The symptoms of eutrophication, such as excessive
macrophytes, blooms of algae and fish kills may result in greatly decreased
recreational, municipal, or industrial use.
Control of algal blooms must ultimately involve a reduction in external
income to the lake. Experiments with algal assays (e.g., Miller et al.
1974), in si_tu enclosures (e.g., Powers et al. 1972), and whole lakes (e.g.,
Uohindler, 1974) have shown that in most instances, a reduction in phosphorus
concentration alone will bring about an algal bloom decrease. However, a
means of macrophyte control, a more important nuisance than algae in many
eutrophic lakes, is less well understood.
While there are few well-documented descriptions of the response of lake's
to nutrient diversion, in those cases where diversion was sufficient to result
in a large reduction in lake phosphorus concentration, the lake-; nave exhiL-it-
ed measurable improvements in quality (e.g., Edmondson, 1970 ;-,s measured by
changes in plankton abundance and productivity.
Most, if not all, of the reported cases of nutrient diversion have
involved the control of point sources, such as sewage outfalls. Perhaps a
more common problem affecting hundreds of communities in the United States is
tne eutrophication of smaller, often kettletype lakes, surrounded by dense
urbanization. Typically the homes are serviced by septic tanks and are
located on small, completely cleared lots close to *~he lake --.hore. These
lakes may have been somewhat eutrophic from their naturally r i r- s-;[£, k ,,t
became culturally eutiophic, with both algae and macrophyte pioMems, liuiv a
combination of septic tank drainage, ^rosion, storm run-off, and other non-
point sources.
Will these lakes exhibit reduced symptoms of eutrophication if one of
these several nutrient sources is diverted? One objective of this research
was to address this question through long-term monitoring of the degree of
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eutrophication of two small lakes after the diversion of septic tank drainage.
Several techniques have been employed to accelerate lake recovery after
diversion (see review by Dunst et al. 1974). While some of these procedures
are directed toward nutrient removal (e.g., flushing, harvesting) most are
intended to control internal sources of nutrients. Mortimer (1971) and others
have viewed the anaerobic, hypolimnetic sediments to be a potentially signifi-
cant source of phosphorus. Stauffer and Lee (1973) have presented evidence to
show that at Least in large lakes such as Lake Mendota, thermocline erosion
and co-occurring transport of P is significant in maintaining the algal blooms
in the epilimnion. The second research objective was to determine whether or
not the application of aluminum sulfate to the hypolimnion of one of the two
lakes to control internal phosphorus loading from the sediments could accel-
erate the lake's recovery aff-»r septic tank diversion.
The organization of the presentation of methods and results in this
report includes two principal sections. The Materials and Methods; section
describes the hydrological and 1imnological methods and a summary of our
approach to aluminum sulfate dosage and application. The Results; section
contains the basic findings of both the immediate and longer term effects of
the alum treatment and a description of the results of septic: tank diversion.
However, since a significant portion of this research dealt with a £;tep-by-
step development of aluminum sulfate dose, effectiveness, and tests for
toxicity,. a description of these findings is included as an Appendix to the
hydrological-limnological findings. Thus the reader may turn promptly to the
procedures, results snd conclusions with a basic understanding of the aluminum
sulfate methodology. Those who desire a more detailed statement of the basis
for dose,, or a step-by-step summary of how to ascertain dose, may refer to the
Appendix and also to Kennedy (1978) .
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SECTION 2
CONCLUSIONS
A prompt return of groundwater, streams and lakes to near zero fecal
coliform levels occurred after septic tank diversion. Leach fields, even when
installed in ideal soils, did not operate properly and their use near lakes
should be discouraged.
Diversion did not bring phosphorus income to an "acceptable" level
(Vollenweider, 1976) over the five year post-diversion monitoring period
because the lakes received untreated storm flow and run-off from diverse non-
point sources typical of urban areas. Lake phosphorus concentrations remained
at levels typical of eutrophic lakes. After an initial reduction in the year-
following diversion there was little change in the algal standing crop.
A maximum hypolimnetic dose of aluminum sulfate effectively retarded
phosphorus release from lake sediments for at least one year. No adverse side
effects were observed.
Net internal phsophorus loading was only partially reduced by the
hypolimnetic treatment. The untreated upper zone of the lake, probably the
littoral zone, was a significant internal source of phosphorus.
The alum treatment reduced epilimnetic phosphorus concentration anci
algal standing crop, but both remained within ranges expected in eutrophic
lakes. The treatment appeared to alter the dominant bloom species from blue-
green algae to co-dominance of blue-greens with dinoflagellates and diatoms.
Hypolimnetic aluminum sulfate treatment may be more effective in lakes
where vertical entrainment of phosphorus-rich hypolimnetic waters is a
dominant internal source of phosphorus. Such lakes are likely to be large anci
treatment: costs may be prohibitive.
Septic tank diversion, unless accompanied by storm water control and land
use regulations, will not bring about greatly lowered symptoms of"
eutrophication. However, diversion is essential to prevent the situation from
becoming worse.
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SECTION 3
RECOMMENDATIONS
Most lake restoration techniques are aimed at control of internal
phosphorus loading. Contrary to expectations in this study, an important
source of internal phosphorus loading appeared to be littoral in origin.
These sources need to be identified and the use of aluminum sulfate tc control
internal phosphorus loading confined to those lakes where sediments are the
primary source.
The role of groundwater in lakes should be farther investigated, includ-
ing studies of nutrient transport across the mud-water interface. Methods of
measuring groundwater flow and knowledge of the distribution of gtoundwater
flow over the lake bottom are especially undeveloped and require further
study.
A land use plan to control non-point nutrieri- sources pr ioi to _ake shore
development is essential. Septic tank systems, even where soils appear to be
ideal, should not be used.
Where lake shore development has occurred, protection of the lakes will
require, in addition to sewage diversion, a plar to prevent fuitnec develop-
ment on the lake shore and to control non-point sources such as erosion and
storm flows.
Macrophytes, which are at least as important as a]qa» nuisances in the
typical smaller eutrophic lake, should receive increased attention with
regard to both means of control and their role in en«ryy flow and nutrient
cycling.
Continued monitcring to assess the long-term effectiveness of *~he hypo-
limnetic treatment of West Twin Lake in controlling internal phosphorus
loading and reducing lake concentration is needei.
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WATERSHED C'HARA* '. ERISTICS
GEOLOGY
The Twin Lakes Watershed i-. g la.-ia1. dr if' >vci iyir. ; '
sandstone or shale bedrock. The flit-lvi:ui ,'ie.r JCK sf-~ita w-c
a pre-glacial stream, and the le.sul'jny t.op'^yrup.'-1, io a vi.J0?
and 2 kilometers wide, enclosed by walls ''-f sand^t-one and ijh-i;
has been completely filled with glacial irift. Figure J i--
section of the buried valley in relation '-:; th" ''V: M Laker.
The oldest bedrock is the Mi:-sif;;;ippia'i-;>e,",-.ri i.in shal^
present only under ti'« drift in the dpppesf car' =i "lecdc 1 !;.'- i
pian Cuyahoga Group !:F.C; abi-ve i lus lv>r t-1 >-; r
Sandstone forms the ippo- part ' > !i «,-
Mississippi an and O.---,, .n: ^n ~; . ^ w--s-, ; -, - i
Illinoian depo;;itK ci-uct i se: >''- ' ',
gravel unit is the p r ''ic i pa". a'|,i.'.' " , ' .
Twin Lakes Watprsh^c
Overlying the I l ; moi ar. \- \.:~-, ',,
Mogadore Till (W-inslov. j'.d W^itf, i->>, - y-
is a sandy, silty, .--tlcareous * . . i , ci ^ . - * "
southern arid eastern p.irt ot t.ri< wi'-i ,|-ic,< (j- '
Till is overlain by in t am Till, i j> ^;- - i i : -. ( ^ ,-
The Twin Lakes w'af et ^«- ! i.*- v,, ' ^ : . -
Moraine of <=arly Wis<"o..nin a-'jc-. Hi* , .; ' ' *.|
formation of kettle ci«-'pr»s.'; Lorr. . pa- it^.- '- - < *
gravel. The settles t .-'.-^m-' ri- ( i :
ice arid <~ruis dev^lopo : p-)r: i i
the.ce Kerv I't i I \<>\>' ><>':
Th<-j pf iricipal >'-< i type, <
upland >jravel and sacd
lowland pea*: and muck :
water holding and t:-si
Ravenna si.-;, is on thf-
erosion and havr-- 1 ->w
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; o
o
O
Z
O
LU
Q
oo-n
E
o
o
-------
\ '
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Chili soils on the south of West TV,. . -nd around the edges of East Twin are
less susceptible to erosion and h-r, .-. ".igh infiltration capacity.
The relationship of the i~o\ i '
problems was not considered in tru-
type soils are not suitable (or .->op,
permeability of the ?ubsoi1 (Pitch:
suitable for most septic systems r>ec
through subsoil. Carlisle r> -. K, :ind ;
leach fields ->e?ause of :.. ;r, v^i
: * i.- tap.K installation and subsequent
an ,-/-dt ion of the watershed. Ravennat
.-ink installations because of the low
>,,d PowelJ, 1973). Chili soils are
>e they may perreit effluent to pass
it so^lr-. are1 not suitable f<^r septic:
var,lf oondirions.
CULTURAL DEVELOPMENT
Ear 1iest reeon
;8i'n five f, ami lies had established
farms in the Twin Lakes area (Brown, 1885; , Population changed little during
the next 100 years. Tax maps filed a1: the Portage CouTty Courthouse (Ravenna,.
Ohio) since 1850 show a change in land ur,e from farming and woodlands to
pasture (Table 1} .
Table 1. I AND USE IN TWIN LA.OJS AREA, 1850 to 1880
1880
Plow
Pasture
Woodlot
Land used
bb.0%
266.4 ha
; . 90
From Otter so--., 19'M
At '"he turn of trie cenfi rv, upveiope; °. K '.qtiC .ne larnu; 3'irrourding the
lakes and by 1918 !!"> major Lo.bdiv i sions ar >un>1 t.ne lakes had been laid out,
and the shift froni ii.ral to ' ^-.ic?e:u:ia; '..<"-'. nad begun. Today there are 374
houses C'n the Twin Lake:- Woor heri. '"" >r.q i-s 'i\7crago of 4,2 persons/home
(Statistical Ab.u r :sc,t ,b oi th-^ I'r., t oci Slit-::;, .'''; i , there- ore 1,571 persons
and c popular ion d'-nr,' - .- of ",,,! -': son j ,^-; J1-1 'o r- .
LIMNCLOOY
I'n>e piiru"ipa; ' { pr,r,log L "n i
Twin Lakes are s-ir''i'^ : ?«d in Ti
are for 1 9"' 2-19 '6 . A r.:or« roinph
al. ; 1 T' 5 1 and WaMer
di.
'in.d hydi ,.] o<;iij j 1 l^aturer- of East and West
* 2 and "illustrated in Figure 3. Averages
e desciiption ri>,s been presented in Cooke et
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Table 2. LIMNOLOGICAL FEATURES OF THE TWIN LAKES WATERSHED
Latitude - Longitude
Area of watershed (ha)
41°12' North; 81°21' West
334.5 (including lakes)
West Twin Lake
East Twin Lake
Lake area (ha)
Maximum length (km)
Maximum width (km)
Volume (M~ )
Maximum depth (M)
Mean depth (M)
Elevation (M)
Subwatet shed area (ha)
Area of other lakes in
subwatershed (ha)
Mean water residence (yr)
Mean area! water load (M/yr)
Subwatershed copula* ion
34
0
0
14
11
4
318
233
15
1
}
1L24
.02 (30.22*)
.65
.60
.99 x 10 5
.50
.34 (4.4'j*)
.73
.02
.00
.28
.50
26.88
'.' . 8 5
0.50
L j . 50 x 10 3
12.00
5.03
318,42
101 .48
3,00
O.S.j
'"* t
,5-7. **
*iShal Low canals are contiguous with West Lake, but are excluded
a-; part of the lake in averaging some 1imnological features.
**Includes the population of the West Twin subwatershed
since this lake drains into East Twin.
Both lakes are dimictic, second class lake? (defined t>y Hutchinson,
1957). In this report, seasons were based on water temperature as follows:
winter i4c Cj , spring (unstratif ied) , summer (mer.al imnion present), and fall
(unstratified). Ice forms in December and remains until earl/ March. The
1971-76 average onset of summer stratification wa^ 15 April fo> both lakes,
and the average summit lasted 210 days in Bait 'IVin 198 days tn West Twin, By
i: - ,1-N- "'mber , both UiKes had circulated.
Dissolved oxygen is rapidly depleted f >!:. i .- v» a:-n -, fc/1- -win^ the onset
of summer stratification and partially depleted a; te: ice ': >r T'I r !.'., ,-..-. 70-
ciated with thermal and dissolved oxygen stratification is a marked stratifi-
cation of phosphorus and nitrogen forms. The annual ra-ge.= of nitrogen.,
alkalinity, pH, conductivity, and transparency are listed in Tatue 3. Changes
in phosphorus concentration with depth and over the seasons at < described in
the Results section.
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-------
Characteristics of the littoral, sub-littoral, and profundal surficial
(upper 2 cm) sediments were studied by Lardis (1973). Littoral s;ediments
contain mainly decaying vegetation, shell fragments, and allochthonous
debris. Sublittoral sediments are brown to black-gray with lesser and varying
amounts of decaying vegetation. Profundal muds are black and very fluid. The
organic content of dried sediment samples ranges from 14% in the littoral to
about 40% in the profundal. The organic phosphorus content of the muds
increases with depth of overlying water and is significantly (p <.05) less
in ETL (mean=66 yg P/g) than in WTL (mean=85 yg P/g). The phosphorus con-
tent of profundal muds declines after the onset of thermal stratification.
The flora of the lakes are dominated by a large macruphyte community
which covers about 25% of the lake area (Rogers, 1974) and by a succession of
phytoplankton blooms. Potamogeton crispus is the dominant nacropTyte in
April, May, and June; late summer growth is dominated by dense populations of
Elodea canadensis. Char a vulgar is, Najas ^fl^iLlS' an'^ Cerat.ophyllum
demersum. After ice-out a bloom of diatoms, usually Fragilaria crotenensis
and Asterionella formosa, occurs, followed by an abrupt change in April or May
when high water clarity and low plankton density is typical. Oscillatoria
rubescens, common in the spring, is the dominant species of the metalimnion.
In the summer a series of blue-green algae blocins occurs, culninat. ing in a
heavy bloom of Aphani:zominon flos-aqaae or Andbauna limnet^ca in August and
September.
The zooplankton have been studied by Heinz (1971). Large populations are
found in spring and fall, dominated by Daphnia g_ale.ata_ mendotae and Cyclops
bicuspidatus thomasae. The bottom fauna have not been examined quantita-
tively, but appear to be dominated by Chaoborus. The fish community is
composed largely of members of the Centrarchidae.
12
-------
SKCTION ~>
MATERIALS AND METHODS
HYDROLOGY
The equation for j hydrologic equ i 1 ibi * urr< wi- .K-i"d in mo.i;-ui e the wa'-i---
balance of the lak>^", from 1972 through J9~<'< . If wa ~ a~,s'in>Ml that the
following ^qjation n ; ris^nre <-'~i. t> /"-n :
uifl'i* -» ;>-H-I :.; ' .u j ' outflow » ;.*']*;" in st.or. age.
Inflow was incoming ": Breams + groundwat^r -t overland flow, and outflow was
outgoing streams t -.nation + groundwaf-;--
Precipitation w< .:. - , .< .-
located on trip north ->.df of f;,- : -!,
shown on Piyu-e 4, ;;--t,i WPT^- t, ' r- *
Rockwell and from "it (8 K;.
precipitation was takp-i from thf H i > ar; ^M - x''n-T*-^- .'H km nortr.
Twin Lakes. For 1974-""6 precip1.' a* iu-. j* ' w !.-, .:, - ai-. r."w
Evaporation was r--, t imated i" ;^v. -«-,'-,. .- ->. \ ,
temperature from the H;ram stat; ' ' .'-' tr--J <'l e-..:p"tv
with a recording evapnr imet^r ar: ; : . 1- - A -
was placed near the lake for the r,;." -Hi, -- >;;"
gathered during periods of freezing temper-at :;<_-.. ' ' ;
installed on the roof of a low building in Kent , F'-r tn^ ',f?a;c 1975 ar. , , <
evaporation data from Coshocton, OKif, 160 *rf sout 'f« of th*"- writ et shed, w t-
used.
The overland flow from indivi }'>: ' pr^c 5 t-i ' -it- j on pv^:it:-, was .ompure.-
using the U.S. Soil Conservation So; /ice recrmi.jut' jio-.rj ibed by Mock UK {!96!)s,
This technique is based on soil v:-M I tra1" ion c;h<,raet ...r i bt ICB, b--day
dent precipitation, and land us--. N'c ict'ial rri" >-'-, u en'-n^s >">t -v-erland
were made.
Surface flow int.- West Twin, Ea-i* Tvvi!., K ;: :>;, -; TJrv;-- ( i,jur 1
measured at 14 stations. Flow it si< ^t.i' . T. ; wa;; p>-; *.- , 11 -, i
continuously monitored at three lo; .if ;or.-;. Tai-T- 4 -ji.'f,- tv^ -1 - ea : "
type of flow, and measirinq fechsaqu^. Th^ f ^C'.ri i q ;- mpl ;>%"-- : ^ r~ !<-.'...-
by the flow regime CM" trie stream and the strewn, gradient. Srrean1 S
perennial stream d; ~.- 'harqing ft >IT We^-.t 'IV'' ' '-'" w i rr.or:.'
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-------
continuously because of low gradient. This stream connects West Twin and East-
Twin Lake, and on occasion during the dry summer months the flow reversed so.
that East Twin Lake flowed into West Twin Lake. Mo structure was built on
stream 5S because of flooding potential in and around this shallow channel low
gradient stream. Flow into Dollar Lake was monitored because this small lake
is separated only by a SjD^agjutm marsh from East Twin and thus is part ot" East's
water budget.
Five streams, IS, 2S, 3S, 4S, and 5S enter West Twin Lake. Three (IS, 28,,
and 3S) , which account for 50-75% of the annual strecim income, were measured
continuously or at a minimum, weekly. Two streams, 4S, an upland man-made
lake outlet, and 5S, an urban stormf Low channel, were measured infrequently in
1972 and not at all in 1973 and 1974. Their 3972-74 flows were estimated by
regression equations based on data from 1975. Tie estimate of 4S outflow in
.'2-74 was obta 11
to ! oat
dail<
outflow? which
s unlit:* - ? . : j
spring ... UC1 ';'
constant pro-por
outflows
sion of
by a seasonal linear reqiession of its daily 1975 outflow
j'f. --w fiom strta.T> ';.-, Br !TI streams are upland lake
4 ; " v.':r;t Twin. The co: : e Lation coefficients were:
:-i, and spr ing
000 M3 /day, r = 0.690; and
Str >-.:
its 1975
!/ r - O.oOJ. A inter outflows of 4S were assumed to be a
of the outflow cf <3. based on the 1975 ratio of. winter
'16 urban drainag--, "--ar, o < Lmated by a log-log regres-
_ ; , fu-w against en' iy7- nyr.thly flow of all other
streams entering West Tw :
flow of all stream- i'i t t>e w.it.-
Cha.ige in la<^ wate, level'-
the data used to estimate ohanqe
' i l for all so-;
J was -.IK- a. sure
-_>? G; . In 1975 the rate of
continuously or daily.
"i water level, recorder and
t ne
To determine groundwater cct.t r itiution t
lakeside wells and in-laKe piezometers w.j?, n/
drilled Ln the waf :jr shed tr .-icinr r.\ ii.e the elt-v.
wells established Ir.ut yrounciwas er flow war; to^aids
conducti vit ies were d^tfrmi ned o'i each wc-II ;.". .r. ; -b
(Ferris et al,, 1962). In 1972 and 1973 an vid>t.r-n-,l
20
ttie
silt
near
kea, a combLnation of
r, "' S "i I 16 WF- 1 I '.-. were
:u nju-jt: . .-
we 11 s w<;i t -Ji- ,- !>
ahore; wt'lls sh'V.,t
an
and clay layer. Shallow
the periphery of the lak<:>s. St atjyraphy
upper lo;yer of saturated sand overlying
groundwater flow to tne lakes was assumed to be tne water passing through the
upper sand laytr into the like. The hydt'iuli- -jradient was; determined from
the water table elevations at tne pnieatic divide and trie elevation of the
lake divided by the distance from the lake to the phreatic divide. Each lake
was divided into 16 "pie" slices (Cooke et al. 1973), and total shallow flow
was the sum of the flow across ^ach of the slices. Measurements of tne water
table levels at the divide and at rne lake showed only Tiinor monthly
fluctuations so the hydraulic gradients for ^ach .il ice were assumed constant.
Hydraulic conduct Ivi tier, for the tested well-, var ied by less than one third o£
an order of magnitojo, so -i constant value tor hydraulic conductivity was
used. The seepage val'.if determined for West Twin Lake was 1.96 M3 /day and
137 M3 /day for East "Twin Lake.
16
-------
Deep groundwater flow was computed by installing two deep piezometers (13
and 6 meters deep) into the aquifer beneath the confining silt layer. Using
the hydraulic gradient determined from these two wells as a vertical gradient,
and the hydraulic conductivities of the surface, seepage flow was computed for
the area of the lake basins. These values were 646 M3 /day for West Twin
and 535 M3 /day for East Twin. These values were used in water budget
computations in the first published reports from this project (Cooke et al.
1973) .
Szczepanowski (1976) attempted to verify the flow rates into East Twin
obtained from lakeside wells by installing piezometers in the lake. Thirty-
two piezometers in 13 nests were installed to depths ranging from 0.63 to 17.5
meters below the water surface. The deepest penetration into the lake mud was
8.5 meters. His data gave an average inflow of 207.1 M /day for East Twin
Lake from both shallow and deep systems, a value 3.2 times lower than that
computed using the flow net technique. His rate was believed to be too low
because deep spring flow was not measured.
Analysis of the water budget and the lake outflow of East Twin suggested
that the values of both 672 M3 /day (137+535 M3 /day) and 207.1 M3 /day were
probably too low; a high residual inflow value could not be accounted for. In
1975 daily stream monitoring and careful analysi" of storm flows, precipita-
tion and evaporation still did not eliminate a high residual.
Ovei the five-year monitoring period groundwater inflow was thus esti-
mated ny the use of lakewide wells (Buller, 1974), piezometers (Otterson,
1974; Szczepanowski, 1976), by the use of thermal gradient and seepage meters
(Cooke et al. 1975), and by lake water balance residuals (Cooke et al. 1977).
A comparison of these results is given in Table 5. No single technique proved
to be entirely satisfactory in determining the groundwater inflow component,
and the rates obtained varied by over an order of magnitude.
Table 5. RATE OF ANNUAL GROUNDWATER FLOW INTO THE
TWIN LAKES, COMPUTED FROM FIVE TECHNIQUES
Method
Lakr-wide wells and flow net-
Piezometers in the lake
Thermal gradient
Seepage meters
Water balance residual
Rate (M /yr)
2.5 x 105
7.6 x 104
3.6 x 10
9.1 x 105
1.1 x 105 to 7.0 x 10'
17
-------
In contrast to all earlier reports of the water-phosphorus budget of the
Twin Lakes, the monthly groundwater inflow in this report was obtained by
assigning all residual water income from the equation for a hydrologic
equilibrium to groundwater. Measured groundwater flow rates were not used.
If the va.lue was negative, it was assumed that waiter was lost from the lakes
via groundwater. This technique was chosen since much of the residual was
probably interflow wnich was not measured, because there are numerous deep
rprings also not measured, and because accurate measures of surface flows,
particularly in 1975, were obtained. When an alternative method was errployed,
as wv; - dene in Cooke et al. (1973), Cooke and McComas (1974), Cooke et al.
(1975; , an-J />i.;ller et a"- , '1976) , then the monthly residual was assigned to
overland flow, givm*: *: - -.-v.ponent of the equation an unrealistically high
flow.
The methods em;, lev, .1
phot us, col if or T bacr.er;--'
LIMNOLOGY
Each lake was
time of ice-out
through the wln.-c-r
Temper a' > >: . "
using a YSI res I Starr:
diameter Secchi ciis,. ,
to the nearest. ; ,1 M, a,
at one-meter uiterv^aS
glass-stopptreJ BOD bof
tion bv the at ice rnoq . r
:"-loal analysis of incoming water (phos-
r i L-ed in the Limnology section.
i> over the deepest part (Figure 3), from the
:;/ing until ice formation, and then weekly
by ice conditions.
\ji - ' to the nearest 0.5° C at one-meter Intervals
<-- r a orne t e r . Transparency was determined with a 20 cm
. '.lack and white alternating quadrats, and recorded
rj'^d from three readings. Lake water was collected
,t'< a 1.9 1 Kemmerer bottle and placed into 300 ml
i'^:-' fjr determination of dissolved oxygen concentra-
r-'Mon of the Winkler method (APHA ]965).
Lake w:-. ,; ;diupu--- ,-.'ei e also collected at 1 M intervals, placed in acid-
rinsed polyevhylent- bctv.l?s, and returned to tne laboratory T^-r physical,
chemical, 01 Diologicai determinations. The following determinations were
per formed on whol^ lake water: conductivity, pH, alkalinity, total phosphorus
and alkaline phospK:* a-;e. The following were performed on water filtered
through a Whatman GE'/A glass fiber filter: total phosphorus (to yield a
"filterable total phosphorus" (FTP) estimation) sulfate, and aluminum.
Conductivity was determined with a YSI Model 31 conductivity bridge, pH
with a Corning Model 7 pH meter, and alkalinity by titration of whole lake
water with 0.02 N H2 SO,* to an endpoint. of pH 4.ir> (APHA, 1965). Soluble
reactive phosphorus (SRP) was determined by the Murphy and Riley (1962)
procedure on C.45 pm Millipore fiitered water 1USEPA, 197L). Total phos-
phorus (TP) was determined by the above colorimetric procedure, following
persulfa~e-sulfuric acid digestion of unfilterecl water (USEPA, 197L). Fil-
terable unreactive phosphorus (FUP) was calculated as FTP-SRP. Alkaline
phosphatase activity was determined by incubating 2.5 ml of whole lake water
with 0.3 ml (0.1 M tris, .01 M MgCl2 pH 9.0) aid with 0.3 ml (0..3 mg p -
nitrophenyl phosphate/ml). Activity was determined as the rate of increase of
18
-------
absorbance at 395 nm over four hours, measured in 1 cm cuvettes (Heath and
Cooke, 1975). Sulfate was determined turbidimetrically (Hach Chemical Co.)/
and aluminum colorimetrically (Hach Chemical Co.). On these tests the results
were compared to our standard curves and not those provided by Hach Chemical
Company.
Total seston was determined gravimetrically by filtering 500 ml of lake
water onto tared Whatman GF/A glass filters, air dried at 98° C, and weighed
to the nearest 0.1 mg without ashing (USEPA, 1971).
Chlorophyll jj wa-o determined by filtering 500 ml of lake water onto
Whatman GF/A glass filters and extracting with 90 percent Mg C03 - buffered
acetone in a tissue grinder {Long and Cooke, 1971). The trichromatic method
of Strickland and Parsons (1968', was used without acid correction. Often
samples were filtered and stored frozen before grinding and extraction,
Phytoplankton ceil volume was measured by filtering 25 ml of lake water
onto 0.45 pro Millipoie (HAWP) filters, These were air dried, cleared with
immersion oil, and cells counted at a magnification of 140X. Eleven Whipple
fields were counted. Approximate geometric shapes were used to estimate the
cell volume (McNabb, 1960).
Coliform bacteria were determined by filtering 100 ml of lake water onto
gridded 2.5 cm Millipore 0.45 nrn filters. These were incubated on sterile
EMB lactose agar at 30° C for 24 hours, Coliforms were identified as the
"metallic" colonies (AtHA, 1965).
ALUMINUM SULFATE APPLICATION
Although aluminum sulfate (alum) applications to eutrophic lakes have
been attempted (e.g., J.O. Peterson et al. 1973), additional studies of
effectiveness and longevity were needed, and the dosage guidelines also needed
evaluation. Our objectives wes e to establish dose determination method?,
develap application methods, and then evaluate effectiveness, toxicity, and
longevity through laboratory and field experiments.
Aluminum sulfate has been used in the clarification ot water supplies and
in the removal of phosphates from wastewater effluents. Dosage is commonly
determined in " jar~ter;ts" in which stepwise additions of alum are made to
determine the minimum dose at which maximal removal of either suspended solid?
or phosphorus can be achieved. Effective dosages used for tne removal ol
phosphorus from wastewater are expressed as aluminum to phosphorus molar
ratios since theoretically one mole of aluminum is required to precipitate one
mole of phosphorus as A IPO,, (Stumir, 1964;. In practice molar ratios of ] *:
to 2.0 are common (Nesbitt, 1969:,
S.A. Peterson et al. (1974) suggested that the calculation of aluminum
sulfate dosage for laKe treatments could be based on molar ratios and reported
maximal phosphorus removal (95%) from algal assay medium and pond water at
molar ratios of 3.0, 4,0 respectively. Such a method places emphasis on the
19
-------
removal of phosphorus from the water column. do'.vevei , the success of any lake
treatment will depend on the amount of alum added aacl trie .luility ot the added
alum to reduce the release of phosphorus from anoxio .sediments, and only
secondarily on the removal of phosphorus from t.v- -vater -joljmn at >:he time of
application. Accordingly, an alternative .jppLo.ju-n u> Jo ., e ja I... ' --it ion was
sought.
The reaction of aluminum with caioonat'c
formation of aluminum hydroxide. Since most. --,.;-_
tically alkaline, dose can be based on tm s .->.,
A12(S<\)3
3Ca , HCO,
a L'. t,,-.» alkalinity is
removedr pH values fall, and dissolved aluminum joncentiat ion begins to
increase. Phosphorus in the water would be i eiuoved b> ont i ipaienf ot par t L
culate Tiatter in the polymerized amorphous alunu Kim h\dr-':
adsorption of dissolved inorganic phosphorus t.,
(Lea et. al. 1954) during sedimentation, 'v
phosphorus in the water column prior, to c; e.
efficiency of the hydroxide, the resulting t .,.
could continue to be effective by retain ing on.
thus produce a "chemical barrier" over ano>. i-
reservoir of phosphorus in sediments tathui
column at the time of application, this appjoa
a long term means of improving water qualitv o
release of phosphorus from sediments.
.hat qed
.-.! J i rig .. j- >;
..iien t .ill
l
on
the amount
n - ""16 L ^itiOv'a 1
-iz-. ;-jimen'_s
sed uuents an J
.. ed . J'nai. do the
C tti t. , - watei
pub i L -. 1. 1 1 ty of
'ia ! I -> jj i'ig or
A step-wise experimental program to ^aij^L.in t
determination involved laboratory studies ^, -rv-
phosphorus removal characteristics,, controlled i .
laboratory and field toxicity sutdies, and the i., 1 l
small lake (Dollar Lake) . These expec unento a. -. -.>
described in detail in Wilbur (1974) and Kennedy
and
xpet i.nents,
-itment Jt a
It was found thait maximum aluminum ax
residual dissolved aluminum concentr atiuii
Ever hart and Freeman (1973) report: can t>e
related to alkalinity and could be det -.
determination for West Twin LaKe is dci^;; -
<->.! =
i .-i t
-\ I
O jv e Wh L.J:
"a t n= wh I j
i. L i e j L L
The treatment of p:i jsphor us - ap . \,;- ; \. .
aluminum dose and the elution ot the L c. , . «
buffers (pH 6.0, 7.0, 8.0) indicated thai or... ,. *
high (96%) even at high phosphot us concent. , at i.,".-j
floe retained the capacity £or continued on . . .-
sedimentation from the water column. Controlled f
lake water (Kennedy, 1978) and field and labor, i'.
1974) confirmed that long term (104 days; c\)i.ti,.L
eld t>-st.
u ..^ Lill'.iiu
« . . . > ". . -i.>h_i >e
--'-' - i
1 > and t'iaL the
L L^III : , ( i _,v> ing
v t: . --> L .niino oc
teal, j iW I ItiUi /
i a L . esoe t L oiu
-------
sediments could be achieved with an alkalinity-dictated maximum dose without
adverse ecological impacts. The decision * treat hypolimnet ically was based
on results of preliminary enclosure -xpe~iments (Kennedy, 1978) in while!"
surface applications of alum result'- : " decreased removal efficiency ir
deeper, phosphorus-rich hypolimnet ic . - , and to the desir-- *<> avoid th>
possibility of localized toxicity ptobl-. n tne epilimnion due t "i deer ear<-'\;
pH.
Based on an evaluation of the results >£ these studies, t!,c decision wa'
made to treat West Twin Lake, maintaining East Twin Lak.-;t Twin and, rhrtefore, shou
benefit fro1?, a reduction t,.f pho-;phoi us conc'-ntr it ion in West. Tw
application methods d". loped -dur iri'j trie pilot treat;ne;;k o? _'(
used. The lateral extent of th^ uppei bounder-, of 'he h/pfO'T-,;
at the surface with ruovs and th^ e: t ; r >.;.-;.; -s'\i at -a di.i-io-j .:i»o tteatrn^-i
quadrats of 100 x 50 M. Measur emrrit of thr vf-lurii; of the hyt-« M OTu.s-'i ! p -rri
of each quadrat and then alkalinities alb'iwod trif.- calculation, of the maxir. i
amount of alum >; he applied to .-avh. The application of th<- l'-)9.5'S M
(36,919 gals) of aluminum sulrat- iust above the hypo L imr.ior, iL- M) tequi-e
two specially desiqne:? barge;; wc>ikng 1 ;< "; >';i s d,-i/ t<;r o total s
(July 29-31, 197S;, A :; -.1 !<.-.] d- S'-: : i. : ,o:. : - , -. -], t.->t rnin ^ lor.
and logistics, ihcijfl; ; ,;: o ,..,;.- j ,: )( !-.: , :?',.>'<-, ,- ;=
Appendix, Also incl> i' i > "; . . . riii\^i
-------
t I
lit
: i .!< parts. First,, since it
i . >] lower nutrient concentra-
sphotus loading through the
1 in.'i , evidence is presented
-, ) r phosphor us-limited and
:n concentration. The most
,/a'«r-nutricnt budget. This
M '1 the lake may be altered
;.'-, and so the effect of
immciiiate and longer-term
:, ! «r,ponse of the biota to
i f nal section quantify-
in.ent in a Trophic State
ton in freshwater eco-
ability of phosphorus.
\ £it the ecosystem, the
of organization. Here
^1.-, with the view that
;MOLUS is among the
-]', "< of the planktonic
it iven to barely
-,:Ji Ion to establish
' 'er-t , part icularly
.:pratp (measured as
'.' ', less their 5 jjg
,>-! misted throughout
:el] density attain-
;ier<->d natural lake-
Water contained an
ve phosphorus (SRP)
-------
greater than 10, ITMX r<.,,,i: :-H>r -T. t i -<1 t: i a ' -f-, , <> ,;.; « t.- ;. . >sj.-n' : us limited,
but with an initial weight at KJ (N:!'. .(--,, t »..."i -> . :r-j,< i;n;_,n; p^tentidj cell
density was nitrogen limited. Det em m.a t i-. >r, .;t !,- ; -lariv N NUi. * NO ,+ NO.)
arid SRP w^-i e used * .' 'X.-unine th1" Pw i n Ltik", N;1 i-T ' i -K.-ri M_ d j - ; o this view.
Taole 6 pro\')d^s v.-i 1 ,f-:-, I -r 1^7, . } \ *) ' < t.. iril*. ,-'\-(^ - i; w-iirh N(; , wa'i
determined/. ci'" n lj-,<-s in eac;, y. -,r i;-} -.!:'->d >o r'> pho.';ph>M 'j^- I united Lskf'i
from thesf consider (fion.s. 'this '.;nr' ,:- i. -i "j;t :,p svqarded cautiously
becaase if is rr r i;t,ii!, ITM' t:;1' lit: ' -v ; : *-K>jd w^-iI-J yield sjmilar
results in the fielii in i i « -!>n; ,<;>. T',f . tf.Tt .;,-. i ena,-: t s urn '-a^r icrqr tiat_un;.
Schindl^i ' i.4 ; " ;<»,--,,t !,- <- :qq* ^t i >n,:- -,;yt ;; .1 -ton dyia r; ;-, are nci*- ^;>
simple as ''v vjfw ' - ,it i.'h;:i'id in, i, , : ^i- i i. .;>< ,. ^r''. ;r.,i tpt poir-ts -LI"
that de'Te i.'; ifi 5 f he N ' ra^i'j i r, 1 i"- . : i. --v -r < r ^*, -|.o in ,; ;,-,rp fy.1 stiiioii* -
ll\g bl .'-m - ' v. ,
i 9 / ,-
it I! i> C" i .<<; -
a i/a i 1 ab i . . ,' ' , :
por, i r i >r:--, -'- . - .
197 >> f -tl : -.;:!, -,. .' ,
WE - I1 :'V»; '
'vVl'lt f ', -.;,. .
-------
100
031
I
CL
O
ct:
O
_j
LU
z
CL
LU
<
LU
10
1
WEST TWIN
EAST TWIN
72
10
SPRING IP! Aig.P/l.
100
FIGURF r>. Relation between mean epilimnetic chlorophyll a_ and spring
phosphorus concentration at Twin Lakes. Solid line is line
of Dillon and Riqler (1974a). Dashed lines are 95% confidence
limits.
24
-------
noted in a later section on phyt--.pl JDK r <:
treatment, 197j was a year of heavy aiai ;
The -ffect of additions -' [h"opru.'
individual population- yrow ing -. that. WIT.
phosphor ur, limitation. If the p<>r.,,:;4i; >n .
phosphoi as. and only phosphorus wo.il"! r-
response ;>; the growth of the po;j '. .>' i ,r,
the ust ol certain "indicator Lpr ,-;-"
l^"'l;. A mod if i cat i >i oi tr;e Iv. - . rt^,
ir.nocjl "it ' .«n of: 4X i (t1, ^ ] ] ^ ,'n,l ,, >- ;,:,.,,*
t-. i ep 1 J r i f <'' TP.mpie )' IciKeW'i'- ' ./
thtoU'"j'r y).4: /c "'(r-mbi jne t) it'_o;)*i. ;
,>i ;>ol/prio-'phia* o ' " ; oolled 1 *,;. . t ,
j'j jdu "-":..: ic:d c.r ) I -\ ~i 1 : m ph. v-^j .-'.IT
ie;non:.-; i .it<_-d a pi')^Jtij'_' corieJs: i , net w.
a]<. aii"" :r j^pha t as^ Krtivit/, i!-i.i:,'i' . n,
pl'nkt :, i'-.i Lac-tes ; ip lank tori ma/ '',e ;?, ;i
-------
systems. Not all species are capable of this adaptive response (Kuenzler and
Pert as, 1968;, but those which are may be identified as growing under
phosphorus-]imiting conditions by the appearance of enzyme activity.
Fitzgerald and Nelson (1966) suggest this as a general procedure for identifi-
cation ;f phosphor is Limitation.
This view is complicated by the finding that some bacterioplankton and
phytoplankton constitutively produce alkaline phosphatase, and a number of
zoop'j ankton also may _n> i nuo';cl / release phosphatases directly into the
watef , Therefore detect:on of phosohatase activity alone is not sufficient to
docunc-r.t pho-;pho" j;; limitation r>f tne species producing it. It must be shown
tha*~ th" species producing it does so adaptively (i.e., t.hat. the cellular
')f the enzyme is variable and a function of available
Both East and We'jt T^in were monitored for alkaline phosphatase activity
at weekly intervals from 1972 througn the summer of 1975; water was drawn from
th" 0.1, 2, 4, 7, anrl 1C M strata. Activity was consistently greatest in the
epilimnion, least in the hypolimnion. Also, the majority of the activity was
partioulate 'i.e.,, .retained or. filters) rather than soluble. Passage of whole
lake^ater thiough filters of differing porosity indicated that enzyme activ-
ity was filtered froir the water coincident with the removal of phytoplankton,
indicating that little if any of the activity was associated with urattached
bacterioplankton or was dissolved ; n the water (Figure 6).
leB hydr^lyzed/hr/l whole
u I/ '1 cell volume of species
producing the enzyme i with respect to time (Figure 7: . Only the results
obtained from the 0.1 M stratum are presented. The greatest activities and
the greatest specif i'j activities occurred late in the growing season, and
maximum activities were always coincident with phytoplankton blooms, espe-
cially blooms of A£hjinj.z_qiinenqri f-J^'acruae. Previous studies have shown that
this species is capable of Adaptive production of alkaline phosphatase when
grown under pnosphorus l:m i ta* ior. in laboratory cultures (Heath arid Cooke,
1375).
Because the activity was predominantly associated with phytoplankton
shown to be capable of adaptive production of this enzyme under phosphorus
limiting condition!;, and because the specific activity was variable and
increasing with tirre, it. can be concluded that at least those species
responding in thi.s m.-trn.er were P-l united in their growth.
Eutrophicat ion is- a process occurring at the ecosystem level of organiza-
tion, tut its effect? may be observed at lov»»r levels. Not all. studies
reported here were o.riried out f-x the duration of the project and one (algal
assay) was performed only on E*zi l?win. Even . o, the investigat Lons at the
ecosystem (phosphorus concentration, N:P ratio), at the subcommunity (chloro-
phyll a vs. spring overtuii P) , at the population (algal assay), and at the
subcellular (alkaline phoophatase) levels of organization all are consistent
with the notion tnar East and West Twin Lakes were phosphorus limited, at
least late in the growing ;-; LI volume and chlorophyll.
26
-------
.12
O
.08
LLJ
N
Z
m.04
FILTRATION OF ENZYME ACTIVITY
AND PHYTOPLANKTON
ACTIVITY
/-CELLS
120
LLJ
80
01
10 100
PORE SIZE(iim)
40
LLJ
O
1000
FIGURE 6. Relationship between algal cell size and alkaline phosphatase
act iv i tv
27
-------
q
O
1.6n
Q
d
1.6
EAST TWIN LAKE- 1972
1.2- 1.2
.08-
.04
SPECIFIC ACTIVITY
AO.D./hr./ul. CELLS
ENZYME
ACTIVITY
*- A
AOD./hr.
CELL VOL.. iil./l.
\
-.8
6
4
12
8
CO
_i
_j
O
~3
MAY JUN
JUL
AUG
SEP OCT
FIGURE 7. Alkaline phosphatase activity, specific activity and eel!
volume in East Twin Lake, 1972
28
-------
WATER AND PHOSPHORUS BUDGETS
Septic Tank_Di_v_ers_ioi-.
A small sewage treatment plant was consnj jcteo -.rside : : water.:v_- : '
receive the divetted, septic tank flows. A f<=w homo;, were onn^r-re-1 :< ,
temporary "package" p".ant in 1969-71, but th^ "-.,.,- ; , < \ , / » noiT-'s ; .
before sewage service wei e not connected t.o th( nt-w iteatment Llai't until .J
(Figure 8). About 85% of the home - were serviced i-/ the end .if 197^, and 4,'«
by the end of .1974. All new homes uuilt since st-wage service negan have beers
connected to the sewage lines. There are presently a fev, (10-12) homes, soniv
of them summer cottauf-s, which nav-- r/>t been ;.onr!ei ted.
Effect ~>t L; ' :ersi."ir, - ' Water and Pho.sphoi us Bul'j--'. -
Wa ':j5£ Ludg_t> i'1- and Vv-nt Twin L-i-ct;: ir- -ir image ;a«,e'.:, but their
principal ?.ou:ce~ ' r - - . M >M We 't ;v:;-' v, i - : :riCMme ^... ; at/,'1,*' >--j| i ; equilibrium,
was high for both :,-;-.^5, oai c , , ' "< - ^ei-a :s» jf this la-yt
groundwater income pluy the discha.-q" ' * ~ : trie me >:, water residerv
time of East was about half that of West (O.-iH ',,.,, ,;, :-, , - areal W3f.?r
load, or mean depth divided by water residenc- '.... r'-ii I v MH 1 ? , was
about twice as high f . ' East chars ' : >.v :-, t :H, ' ' /- t
The source of tnt large gr ~ .r.dv, j'-t-r .'.:;c. .m - t . :.:_'. IV
by Szczepanowsk \ ;19"n>. Lake iio. k*t ; I , -u. >:^ ou." .i-:.'-,r -,:: -- -
Twin, was filled in 1915 by damming the Cuy.j'i'.q; '' . ". . . .-
determined that the level of the Twin Lakes rose significantly after <--,:
even though there is a high bluff between Rockwell and East Twin, ana no.
interconnecting surface flows. Szczepanowski installed piezometers in LaKe
Rockwell, where the two lakes are closest, and estimated a groundwat^r
discharge of 800 MJ /day toward.-, Ea,(:t Twar. .
The seepage from Lake Rockwell may have been paitialJy responsible foi
maintaining the lak^ water levels in the Twir i,akef=, ever, after sewagt-
diversion. On other lakes water levels have oft^n dr(jpped ft.-! lowing sewa"^*
diversion. Water income and wace. l^vel oi r,-jtfi«'t lake -. vi^ijed in a w^ ,
which could be atfr :' ''ed to diversion, «v--n r'-'.:,'1 ? '.^ d.i1.".- siori «xc;!,'f."r
approximately )53 M i iy out of t"e water -'«''": *.. > previc^u1 . . n-H
the lakes as over lana i low, stream flow, and gro,,:i-.1^a;.^r .
While the several methods of computing groundwater income to the ia«>--
were in general agreement, the sources of th<=- wat^r we; e net spec i f ical 1 ,
located. During ice cover unfrozen "windows" were observed in both lak-
29
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rt.^nJAl, PHOSPHOPr S ','('<;(> K ; ~,i
SOURCES
19 7 j
1974
197 ^ 12i
1976 12]
suggesting that fairly high volume springs entered ; .< laKet. u'..e wui::d not
be detected by piezometers, so that the rate of -seepage from :.ake Rockwell,
and possibly from the four small lakes above Wr-c;r TV.' . . ",
higher than Szczepanowski (1976) estimated, !h < ,-. r-v. r ^ , , ,.-
the decision to assign groundwatei income r. - )' ^ M :',,', . ,
than depend upon in-lake and lak*n-
sample higher volume springs.
Phosphorus Budget ~ Phosphoi us antes r-d -hi
dry fallout, and gijundwater and stream flov,:., ,
was not monitored.
The annual aveidcji- concentration ot i-ho-;i',.i j .. r.-:
lO'i did ri-it change. The sligritly higher - -' - * ^./u
reflect.*? ':.'-.' m.jcn larger number of detorm i : i* ' , .5" ,-
I.T, i r.gc- - '^r;.;.- ' jturv ,'",";; £. >. or.; «v, r>',l .
fali-'U*- *ac- '} >* iti'^.j:.-.,: - L
A netwoiK ot p^e/ometers was estabiisht . '.- r>j% ;
phosphorus conti ibut ior:s from gr. 'undwater . Tr-- - .-,>-.
West Twis:'s q-'iundwa*. inn < iv-d -r >'7 ''5 ;
1976 were not ai'-r-;' ,-t : jnd were i'- ,iT.t> j
phospho: ur. ,ti i : '. >- FJ,; '*'. ,
10 ;- -'- -.r, x;.. *. , -:..-..: - -
HAS'!1 TWIN
Grojtidwater Stream: Pi >-. ^ 11 a; i.
-------
To determine the impact of nutrient diversion on groundwater quality,
especially in the vicinity of septic systems, a series of monitoring wells was
drilled above, in, and below a leach field. The monitoring network was set up
six weeks prior to connection of the sewers. The boundaries of the leach
field were found using electrical earth resistivity techniques. All effluent
was diverted from the septic system after sewer hook-up, but tha leach field,
by request, was not disturbed, and samples of the wells were taken weekly for
the first two months and then monthly.
important
indicated from this mon
leach field 0,3 ineterr-
the water table was ab<-
from the leach field, *-
(Figure 9) . Tries' .. J
f ield, perhaps ?aur-< - r
leach bed. Thi' "'.,
by soggy lawr ~ o .- L.
washed from t: -. la*",;;
accounting for the K? "
No clay WE,"-' o . ^
coarse sand and : '"i
in coarse san ^ .-i-vJ
leach field -3y-r-, ,.
then contr i b,'t<- -
runoff and o-/-:- ' --,
factors about pre-diver sion phosphorus i;ncome are
itoring. First, the water table was encountered in the
; belo,,' the surface. Six meters above the leach field
'' net'-r,:; below the surface and 3 meters downslope
f.-hle '*as about 2.5 meters below the surface
o : , .- i ,di'~ate a perched water table in the leach
rajs which reduced the permeability of the
"on throughout the watershed, as evidenced
:,, Nutrient-rich materials were probably
- -l and streams, and thence to the lakes,
;nccro(3tions in streams in 1971 and early 1972.
'.<.- area of the test leach field; the materials were
'=-.4; icv.p to 6 meters. Thus septic systems;, placed
(polls which are presumably ideal for septic tank-
i discharge effluent to the surface as seeps which
wnter flows, especially during periods of high
The ch
perched wav-
tion . 'I 'if.>
the Lea-/!- :".
siigatiy r. T-
diversion.
.r , -] of the leach field shows tine effect of the
<? !"->rsion on the groundwater phosphorus concentra-
I. ""h'1 Control well 16C, and the wijll 9 meters below
cry clo5;-? (Fiqurf 10), indicating little phosphorus
n'jMiw'aic-r away iiom the leacn field. Well 17G,
je I d, had a logarithmic drop in concentration imme-
W'-l! I8G, locd^fd at tt-f toe of the field had a
t a t i >n thcin the control and dropped little after
Surface water station *.." (Xiguie 4) is typical of the urban streams of
the watershed where sources include basefiow, stormwater runoff arid septic
effluen'.. Stream 2S received the surface seepage from the experimental leach
field and run-off from an urban area. Figure L1 illustrates the relation-
ship between reduction in water discharge, phos^hoi us concentration,, and the
number of r-.pve. "ontvvc"*. ions fron* ,':,T,uarv 1972 t ti:oi!'~jL Peons.ary 1^73, In this
interval the mean wa~Pi discharge from 23 dropped from r-.Ver 410 M3 /day, to
less than 40 M / concentration from Jun<; through
August 1972 might be due to construction of sewer lines in the area during
these months (Bullet, 1974).
Figure 12 i:
the same period
a plot of phosphorus output past the weir at station 2S for
)f time. The output dropped fcom almost 80 kg P in January
34
-------
35
-------
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0.10
Q-
Z
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o
0.01 h-
1
PRECIPITATION
J
A
0
16G
17G
18G
1 I \ I"
l r* 1
\
i
n
FIGUR3 10. Total phosphorus concentration aK,v«, in,
experimental leach field aft^t d i', <'-. : >;
cm
20
j J 0 ;
36
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UJ 0 '
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M A M J J A S 0 N D J F
PHOSPHORUS OUTPUT. STATION 2S= JAN.1972-FEB. 1973.
MGPM- i? p'<'-p'.,r - "li'---! ', ' '> Mr. MO '"' '" K "' I'win after diversion
-------
1976
-------
Table 12. WATER - PHOSPHORUS BUDGETS OF EAST TWIN LAKE 1972-1976
_ _ _ ,.. ._ __
1972 1973 1974 1975 1976
1.
2.
3.
4.
5.
6.
7.
8.
9.
Annual Water Inflow
M3xl03 (Q.)
Annual Water Outflow
M3xlOJ (Q )*
Water Residence (yrs)
Vol/Q =T
o w
Areal Water Load
Z/T (M/yr)
w
Annual Phosphorus
Income (kg) (J)
Annual Phosphorus
Outflow (kg)
Phosphorus Retention
In-Out
In
Phosphorus Areal
2
Loading (gm P/M /yr)
Mean Annual Inflow
Concentration
(yg P/l) (J/Qi)
2152.2 2056.9 2971.9 3192.9 2614.4
1978.9 1921.0 2515.1 2996.6 2446.0
0.68 0.70 0.54 0.45 0.55
7.40 7.19 9.31 11.18 9.15
180.8 126.8 219.4 213.4 127.4
142.3 109.0 157.4 177.5 135.5
0.21 0.14 0.28 0.19 -0.06
0.67 0.47 0.82 0.81 0.47
84.0 61.7 73.8 68.4 48.7
*Does not include water lost by evaporation
40
-------
1972 to approximately 0.05 kg P in February 1973. Following the rapid change
in total phosphorus in 1972, concentrations in stream 2S remained in the range
of 50 to 70 yg P/l. These concentrations represent, washoff from streets and
lawns. At least one other stream entering West Twin (5S) was also influenced
directly by sewage and runoff in a way similar to 2S.
The main source of phosphorus to West Twin was from streams in 1972 and
1973 and groundwater in 1974 through 1976 (Table 7) . The mean annual
phosphorus concentration in streams in J97/ was vr.-ry high, particularly the
two streams (2S, 5S) draining urban areas rather than those discharging from
upland lakes (4S, 3S). Income from streams in 1973-76 was 50-75% lower than
in 1972 but mean total annual inflow concentration was as high, in 1975 and
1976 as in 1972, due in large part to the increased concentration in
groundwater (Table 10}. The reasons for 'MS incr<-.K -v jr^ n<">t known.
The mean annual phosphorus concentration in the stream <8S) entering East
Twin Lake fell steadily from 1972-1976 (Table 10), with the 19"t concentration
25% of the 1972 concentration, due to the alum treatment of We'-t Twin in 1975.
The concentration of phosphorus in other East Twin sources did not decline so
that the mean annual inflow concentration, as in West Twin, remained fairly
high through 1975.
In summary these drainage lakes received a :; i-jni 1 ; can1.
fronf' -seepage and springs. The quantity of phosphor UK in ":
enters the lake was not measured, but was estimated trorr com,
piezometers on the lake margin. Concentr =jt a or, generally- I' -,'">,-
study period. Surface water flows from urban -v ej;-. wet*.- ,! i'.;'
before diversion, presumably from upward seepage of effluent from
to the ground surface, where it was carried away as rur:-C'j i
Stream concentration fell over the study period. 'Petal ph-s >.', ,
year was variable from year to year and average inflow conc<->r,t L ,
Twin was as high in 1976 as in 1972. (Tables? i! an i 12).
of water
Iwater as it
entrat]on in
sed over the
'i phosphorus
leach fields
to streams.
'..- income per
'.:on to West
Vollenweider phosphorus loading model - Volienweider (197*1) has suggest-
ed that the critical factor leading to eutrophy in phosphor uj limited lakes is
the total phosphorus concentration, a value depending on average annual inflow
phosphorus concentration and the water residence time. Eutronhic lakes tend
to nave high average incoming concentration, moderate residence times, and
generally have a phosphorus concentration greater
weider (1976) designated regions of a phase dia
piv spl;orub concenti -at j,>n vs watei ipsidenc- t J r»t> >
>J i )<'trophir to putrophic, divided by l>ou:i-Li< i
loading" (those whicn tesult in a potential OMKV
P/l) -'if "permissible loading" (those which resuii
less t nan 10 ug P/l) ,
:q ?'l. Vollen-
annual inflowing
.-.ns i t ion from
"excess: i ve
thai, 20 ;jg
Using data from Tables 11 and 12, trajectories were plotte.i with 1972 as
the initial year for each trajectory (Figure 13) . Over the da; .ition of this
study the phosphorus loading to each lake was excessive, and there was no
trend from year to year, other than a small decrease from ;9";.-', to suggest.
that septic tank diversion resulted in a significant decrease towards
41
-------
en
c
H
TD
<0
0
u
0)
0)
c
OJ
0
w
(C
c
4J
CO
C
(0
VO
4J r--
tn o\
(0 iH
W i
(N
u-4 r~
O CTl
M
CO
C -
O g
r-i nj
-u u
H Ol
(0 (0
0 -H
P4 -D
42
-------
"permissible" loading. This observation is consistent with the small changes
noted in mean annual incoming concentration to both lakes after diversion as
well as with the small changes in lake concentration and in biotic indicators
of the degree of eutrophication.
EFFECTS OF DIVERSION AND TREATMENT ON PHOSPHORUS
Immediate effects of aluminum sulfate treatment - West Twin Lake was
monitored intensely just before, during, and after the aluminum sulfate
treatment, and then at weekly intervals through 1976. The immediate responses
of the lake were primarily chemical, and differed from any expected longer
term response in that there was no immediate effect on biotic indicators of
eutrophication in the epilimnior> a:; measured by cell volume, seston, chloro-
phyll, or transparency.
Aluminum hydroxide particles appeared in deep water samples for several
days after treatment, Artei two weeks the lake was examined through the use
of SCUBA. The epilimnion at this time was murky due to an algal bloom, but the
hypolimnion, in contrast to the absence of light in pre-treatment dives, was
clear. The lake botton; could be st,-t,-n from about the 5 M level. The mud had a
uniform "carpet" of aluminum hydroxide floe about 1 cm thick with no bare
spots, and it resembled a moonscape with pock marks where anchors had been
dropped before treatment. There was no floe in water less than 5 M deep.
Later, the floe consolidated with the sediment so that by 1976 floe particles
could only be observed ir, diedge samples.
Dissolved alumi'vjm remained below detection limits at all depths and
locations, with the exception of one sample at 7 M just after application,
where a concentration of 2.4 pg Al/'l was observed (Table 13).
Table li. Pi
-------
The alkalinity and pH of water below 5 M were altered by the alum
treatment (Figure 14). Hypolimnetic alkalinity before treatment ranged i'trvr,
110-140 mg CaCOj /I. Just after application alkalinity at 6 meters was <>0 n .
CaC03 /I, and the hypolimnion below this depth remained at about mat alka-
linity until fall circulation. Pre-treatment alkalintties returned aft.-,
circulation and have remained at that level through 1976. The hydrogen tor
concentration increased slightly in the hypolimnion, nut returned t' ;>; f
treatment levels within a month (Figure 14).
Sulfate concentration in the hypolimnion was increased frcm a pre-
treatment volume-weighted average of 35 mg S0lt /I, to a post-treatment aver
age of 50 mg S04 /I. The concentration below 7 M a month after application
was over 100 mg S0t»/l, and averaged 50 mg/1 during the fall, in ccnc.t ast t.
pre-treatment. fall averages of 40 mg S(\/I (Table 14). Wintei cono !>t rat ion =
in earlier years, as well as winter 1975-76, averaged SC mg SO /!. .Mhimi-"
1976 concentrations were almost twice as high as previous y-v>fs, Th- .< < .-
change in the sulfate concentration of East Twin.
No toxic effects, such as fish kills, were ooserved after the application
and fishermen report fishing to be as good just after treatment and in 19"'*! ,v
before treatment.
The concentrations of phosphorus fractions in West TV/in ',,oke were
promptly affected by the alum application (Figures 15 and 16). Sol ib'.'
reactive phosphorus (SRP) in the epilimnion before application ranged from l-r>
yg P/l, and in the hypolimnion, up to 500 yg P/l. Filterable total i>L :c:
phorus was about 20 yg P/l in the epilimnion before treatment and above 400
yg P/l in the hypolimnion (no measurements of FTP fraction were taken at 8 and
9 meters so that SRP, which was measured at all depths appears to be higher}.
After treatment, the concentration of SRP and filterable total phosphor us in
the epilimnion remained unchanged, but were greatly lowered in rho l-ypo
limnion. The lowest concentration was reached about one week affet ,--.pr,i i <--
tion.. One year later hypolimnetic concentrations were slightly ,.;:-;, ->.,'
were still 10% or less of 1975 pre-treatment levels (Figure *'-,.
Total phosphorus concentration in the hypolimnion was also great';/
lowered after the application (Figure 16) and remained low through 1976 even
though oxygen was absent in the hypolimnion.
Effects on Phosphorus Content of the Lakes - Trie phospnorus concent- o'
the Twin Lakes varied in a regular pattern over each year (Figures 17 and >H;
During spring circulation phosphorus content steadily fell to i:\ ah-r - ;
just prior to the onset of stratification, then increased, ;UOHC >i
increase being in the hypolimnion, to a late summer peak. In some years <
increase continued through the fall to a winter peak. The soiing deei"V:''-
began shortly after ice-out.
The daily rate of increase in phospnorus content over tr.e KUHUK-- u,- > .-- !
became less in both lakes each year after septic tank diversion, excey- ,<
West Twin in 1975 when the interval considered was 40 davs shorter tran of~l:--i
44
-------
O
45
-------
Table 14. SULFATE (ing SO^/1.) IN EAST AND WEST TWIN BEFORE AND AFTER
HYPOI.TMNFTT' AIJJM APPLICATION
Dopt'
(^
1
p
3
4
Vv~ f TW i n !,ak«
.
1 ] ', PP Anq 7S
i, ' ^
" < 4').
' . 6 - 41.
4 . SO 4 » ,
i ^ ; 4 i .
i >;< 4*.
: - (,< .
.'< ' .
80
00
01)
0"
0 '
1 1
' JuJ
;q
54.
49.
48.
48,
47.
47.
76
35
41
97
80
14
7]
27
H
9
10
11
20,47
106. i-
10S.O 7
. ).96
f'9.67
Depth
1 '''. "
/ f 4 i.
i ]'*, r
4 V) H
4
10
I!
yeat.c- (Tabl'"5 i ^ , H;i 1 t [,?» ,-, ,r-. f c>a meri' n- ! ." Mtt i- ni'jIi'M than thp prev;. cm- /ear and the rate thus
equal to 01 1 «-?,-, t ', . , 19/4. 'I **- r ^ri^t \nr, jn thic. t u*1 of summer increase was
particular ly pr->t..^ '. r , ,-t iw,n jn IQ-", and !- /?, (Figure 18, Table 15).
7^,p efff>f-} i,f t )
pattern of p'v -. ',' '
illustrated ri Figui'
peak July 197C> p' p t r
rising S'HTI^W' ->' ;-
Wf"t 'iwin hypolimnot ic alum application on the annual
<'.«,<< ->nd Ui^ hypoi inmetic summer increase is
' "i'"r- ph<^'-;phot ur> content was lowered by 67% of the
trupn'- content, and remained at that level through 1976,
' ""'' :<»7f-. Autumnal 3*i< -'.al circulation did not
increase eitn^r
phosphor os or the alumimim (<-, \< cntration of the lake.
46
-------
CD
or, 4
LLJ
LLJ
8
10
1 WEEK BEFORE
.REACT, P
1 i 1 1
S
100 200 300 400 500
ngp |.
1 DAYAETER . 1WTFK _1YEAR AFTER
.
S
Ot A ? '
8
10
10
6
10
100
i.g.P !
100
100
-------
-.0
C\J Tt (D CO O
Sd313l/M-Hid3Q
o
o
CD
O
O
LO
O
O
CO i?
~J
o
o
<
Q
o
o
M-l
rU
O
14-1
0)
1) T UJ *"^ ^
i O
1 °
J^
^^^ ^^^^^^\^ __^^^4k
^* 4^1 np ^u -f""^^^^^ ^^^
1 1 1 I II
^^
/) ^t 00 CM
Y""
/'
/
y\/
/\f -
/
/
7
/
0
o
CO
o
o
CM=^
oT
7"T
^^<
O 5
0
CO
0)
s
c
M-l O
O -H
JJ
c fd
0) U
Cn -H
>< iH
x a
Oo
M-l
rd
(D a)
> 4J
cH (0
0 <4-l
W rH
W 3
H y)
C it
e
co a
3 i1
6
,c u
to -p
O
-------
200
100
0
200
100
1 °
DC
o
O 100
5
0
100
0
50
0
TOTAL PHOSPHORUS CONTENT
WEST TWIN LAKE
*
.ALUM
1972
*
1973
*-. 1974
1975
1976
T A ' s ' o ' N T
J ' F'M'A'M'J '
MONTHS
FIGURE 17. Phosphorus content of West Twin Lake, 1972-1976
49
-------
150
100
0
100
c/)
o
0
100
0
100
0
TOTAL PHOSPHORUS CONTENT
EAST TWIN LAKE
1972
«*»
* « *
* m
.
197^3
*
. /v "/ 1974
* *
* «.
«
1975
i i i
*
*» *»
1976
JFM A'M'J'J'ASOND
MONTHS
FIGURE 18. Phosphorus content of East Twin Lake, 1972-1976
50
-------
Table IS, RATE OF INCRKASR IN PHOSPHORUS CONTENT
SPRING r,OW Tn SUMMER HIGH grrs/day
Sa ~ t Tw in
1972 7r, i
1973 Mt-4
1974 4-J
i 9 7 S 6 '< < *
I 97b //'-i
*'Jp t") da.1 . i a i "'i -,«>;.' r at l'>r.
-w-- > dhted seasonal --orK-pnt t at ion of the three
phosphorus fractions Curing 1.97 1 - 1L)/6 are illustrated in Figures 19, 20, and
21. Summer means i.')..lude all ia*' strata, ChaiKjes during 197.1-1974 die
discussed first, sin^f- these --h-inq'-s may he related to diversion,
Mean total pfiosf-'1 it UK (Figure J9; -? both iaK.--3 was hjqri in 1971 before
diversion. West Tw!"r, while in.t^ally higher in r wen^ration, exhibited a
steady decline from ''-,'! ro alurr tr^afinen* in il)'!r~, -/,;,lie Ka."t Twin, after a
small drop from 19 ,' 1 ; > i'-*72, r^-ma ou-'J fai'l/ <-,ta.,!'- u -ibout 75 [ig P/l,
Spring mean c"n'"'°''!! : i !>>v. w: ' ' > ~trr\rnjv- ->'' it-e-' r-- ,n epi li rnnet 5''
chlorophyll '.P'lg'J1-> -'na'"^ '< ^t ')-/r, ; ' ' i : ", i -- Twin, whil"
West's dec! :",-- ; \, .. :i" ; , - . f -j r- ' '. : - ; , ^ ,
Mean >:otdi /-ho . ' t ;s '>'! > nt . if -i i- ;r r MM ii fu i a t i >n t.r' both laKe^;
was determmeo ''-.J r-i - :>-<, ^ <!,- -u.( },-,.'. niot phui"0^! /, jr-J A-;(.er budgets.
Predicted pprinj - : . j'i'^n, -< >:.- c" "-J^' f ri!l.;n d-.-i r;ql^r (I974r,,
was always r.igh^. ''. -"r '--', .-- *; l-.'/v -,ti > I9"75 i> '< -t. Twits, nu!
always lowi > , ..!-. :-," i'w i, !-)>'. ,. . H-.-w ^f-: , the .'"rr1;?-
pondence bet.^/^f'- pr .5 ,. ^^ i ;<>'- -. ' -. r ing >> <"oncl MS i'ir,
that pho.'-phor1, - ',<> >? , , '., .i,t- :,. .v>;.: ., t ; i~hi;-g, ;-i,.i i -.*. -?.'M i,)n,
determined : pi i : t .it- ,\ -.- , i>, ,-i.r - 101 ''M,-. appt-ar.'; '. nave !f -~j>f"ir,,! i')f..r r>',,,,c;prioi us ' <".<~ fnt r ^ i ,or -'f
West TV in,
" t .1 ;->i . i.-p'u -rut: KSP) '"oncenti :itlon ;Fi j ;t
w H r: l'"-t7i ,--i'i 1974. j-id apf.'t'ared '" i^f---! .n>" :
" ' i ;. .'. ' i ng -j.;,o ,. i'!unet; I ^ .' ' ;or I-'is^ "i\v j >
were que ;t j ?n-?.' <"-."1 ^^p ,.. WJ-- l !-.f->r - t ore discard-
ed. Mean ;5e i'--.:,- . : - -* .- fi , r- !-. ,":' <-i i. > ;.'. \ j! . >r; wd'~ aim--''
always higher i;", l^> ' : v) r ' : ' ; -r t , it I y i.. ; '') -r ' f-| : , F' igure 2 ; i .
This diffeience jn U>e fall ':'. '..)' : , -^ i- *- > * f;. "-t;'i,.r '{ , it uriin leaver,
and leaf d'-"-oi,.;,' ,,-.>/-.- , . . .,,,,. - j ... _ - . , -, ^er.t Tu-jii
East Twin, it wi i ! : ,-.; ' v ,H .. ,;-,;..,r - ' \", ^-it.-r;pM if from : t r,
subwater shen, ".-, : --, ,-. o:,,, , ..-..,- , r,,: ^« i -_.-;./
unaffected b\ !'
-------
z z
55
k_ h-
QC
(0 CL D <
-------
Mt.AN si ASONA;
100
80
60
40
20
1 O *"» 4 I «
I £ -, > «* ( s
1 9 7 3 l
! Q ,' 4
-------
co<0
IN.,
M?
>£:
f
CT>
'0.'
:s
.»**
5' t.\i v"
-|
4r-
-M
-------
-------
West Twin, was greatly reduced ;i - pre-treatment concentrations and in
comparison to the hypolimnion of E~rt ivin.
Table 17. AVF.RAGE EPILWNl X.r.NTRATl UNS OF PHOSPHORUS
FRACTIONS ( .jg P-l) GLUME-WEIGHTED)
1971
i 9 7 2
i-- in t/.. t il ph<~. .tiriot u.-- i;. t f.(- ;'_; ; i L inin ion of West 'Pwin was
25.5"" If-'-s in Iy76 than Kast 'IVin '2R.j v ~. vi.O :KJ P/'l). filterable total
anri 'u>l' bl^ i '-.net i -f- : ;spli'>iu ' )! die epi ' irurti->n wre only 2.5^* (19.2 vs 19.7
,q P, ,- ^nd i..-*, M' i v-- 8.: fq P/ J ) Less, respectively (Table 18). Mean
annual and ppnmu,. - , - c<.i:c <-!if t at ions of T 1 L fractions after treatment re-
ifu'.:! t--i^ r -.rr^- ^xp-.'t^: ! en trop;, : ,:
The sr, '-i ! : ''fu'ii!-j'i in ^r> > 1 niir.-'t-i . tilretahi" total pho.vpliorus may be of
ome s i 3ni t" i !vm<"" > nice low m'> l--i-'j 1-n we; jht '>r gani^-phosphor us molecules
-------
found as part of this fraction in t>ie Twin LaKes (FtarK'K>_> and H^.tth, in press)
"tiay serve as sources > ( ;-h< 'Sphor us lo son1'.-; jiMo'ipn- " !.', I un i t-r. ,'.,.. q? r.on algae
(Heath and ("ooke, M7''i,
In Burnrnai V , sep tank divrsjon appiien1 ly ;-r vu _ ; --t.ny cifclint- in
mean tot a' phosphor ur, of Weat Twin, and tee nnr i,,q ;i,.i !(-- ; r. in tne Jake
dec] ined '« t)te level ,-.f hast Yw i :,*:-; rpi ipq D'I'-"i t/nr'-.'-. >: v- ^-i , t}i«=- 1475
spring c^n^entr at ion ->s, iit-f. >'< ' n.- t < \;v>! '-;,! . >( f>ut 75
,i j F'. i , a leyo i wh >. <!> woj I i f~: -i-; i. ^ ( ':.-- i ? ; >. - ; ,,-. ' ' , M 'johy : i
concentration of a mod'-.-rdte Ly eu'iopn:-' JM'.I- , ; :, it-. !!-.'; ' -r -," if- Affective
i , low"! JIM f. h<- c-oncentiat ion of pt.i i;,pi,- >i <", ,-..! ' i r i r; i i .-. >, ^ ,j f^njr
yea: p->' t -iijvrir -. ion oc-i iod ti.) l^>/f-;^ wh " v.' ! : t ' . i r , -' ; ITSM .!^<H|t-'n^
in syinf, t-r TV -,j .-it t ,-,,\ i- Ttion,
Intej jijai '^h-japh'1^ us J-o3^i_i_n^j " Thp rt-i^.i1 .>! pir i.-'ph- -s j : ; rj:n x.\c
sediments has L;een commonly observed in hot '< i ihc" -itoty ^ri!1 f >c-\ »xpor irnent =;
arid i« believed t.'> hf i P iyn i f icant in*«'ini! ^,'iir"^' -il ph'-<-,p!' i ^i Th« ani'Xio
sediments >f tne hypci iinni'on of West, 'IV n, > 'Ke wt i * t h^M *>f >r-" treated with a
i "come
ju inea (net i'jlPCi!H>
;'',;'' ;,ft-: i. 1 1'iadin'i f.t'es d"e l 'r,
«,>f a smalJ inc'^aH-e in East IVin's
that ..-f
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r- o r~ rn
t 1C*
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PJ
58
-------
Table 19. NET SUMMER EXTERNAL, INTERNAL AND TOTAL
PHOSPHORUS LOADING TO THE TWIN LAKES (rag P/M /day)
WKST TWIN
Year
1972
1974
1975
1976
1.266 IJfi
AJJJM AH'LK'ATION
1.3?.' 77
Year
1972
1971
1974
1975
1976
7 Si)
LATION
,022
2.86f 98
I'M i 1 ?
1.08b 125
ALUM APPLICATION
1 ,58', 7<>
The 1975 aij" -
expected snarp d- -..:' .-,
Over 50% of * r r -',-.
rate was oiil, . ! r1'
/day in 1976}.
"iMor, t trif hyp-11 j in nori 'iici not result in tht
i'->~f> net internal phosphorus loading of West Twin.
' T-.T-.. .1 ; ^ ( , )- .-)., ) wh»n compared t-o
untreated muds, strong Jy suppcjri- tti^ '><*-} pi^ i rin that the release of phosphorus
from aluni-t r°a* f5-.' n- ' - . Hov/ev^' , t'K-
similarity in mean ep i limner, ic t''t^[ ph.-,',;Dhr -r ];; ; 'iix.'^"' : i : -r betwef-n the
lakes in 1976 ;WTr -- " ^ ; P ', ~'T' - t . , '.'...- ' , --mo t,, - v^rv
lOW hypoli^nno; .- t>,,' ' > -V. ,i i ..- I , i > i ',i, i , j i i ' ,;,.] Vlbjf !H/
support tl'M ; M.I ' . i - i, -! -i - -.ii) -=i' rj hy st uiffer and I.e^
(1973) a:- a -'o1,':- > iiit^'ra! l-v.iiin.j to the ; i I i nits ion, wnr, not of great
significance in M^- Twin La1-'-1'.. -;iq'-1 f Leant p<'utioni-: of the net internal
phosphorus >'( i ---< ' ; -' '' - - .'iL;r. -> ir:;i<-,f 'iave h^p-n f > on- ^o';r< <=.c other than
the a-.af-r'-; i-. ' ' - : . -,.,'., .],, Liit^ in
-------
effective alum treatment and the concentration of phosphorus in the epilimnion
of the two lakes was similar despite dramatic differences in hypoiimnetic
concentration.
Further studies are needed to contirm t
suggest an explanation for other observation
intuitively clear why the late winter - eat i ,' ,
should be strongly related to mean epilimnetic :
Rigler, 1974a;Figure 5), when that phosphorus
during April and May each year (Figures L."
precipitated phosphorus is released as sum,Tt>;
then the strong correlation may be explained.
and the biota of the littoral may be espec:
phosphorus to the water. Macrophytes have Loer
from roots through Leaves to the water (e.g., M<
release significant amounto (Lamarra, l-> '-,-',
strongly suggest that both aoiotic and r;ioii
be the major contributors of internal phi-":in..»i
Twin Lakes.
3 I
-: i-i !.'i.;'lus ion, out it does
For example, i': is not
* ; pr. r.pr.ot UH >-oncentration
i7i<-T '.<<; r )(;-, i i Oil Ion and
'LOC:I ; .'on; tj,c. wu> 't u=i loading,
iina i - : aRes, qroundwater
ly import.ant. iri returning
>wn to :.} an.s}>. . t phosphorus
- PT _ , 19/2; , arid fish may
:'".-:* - ..; >n ,- ".-i others
r ',-: . t - , i L! L zone may
I- a '. '? i n l -Kes like the
The annual phosphoius retention coeft
loading. Kirchner and Dillon (197'5) deveio;.>
15 Canadian laKes which estimated R from t ?v.
Table 2D the R 's predicted i rom tiitir eqiiat. i
Lakes are listed (see also Tables 1.1 and 12) , He
fat lover tnan predicted, which means that
-------
Lakes with a i-\-\' >n-.j'jn L i . t < t \, .:>! i> ji, ;: , ;
"saturated" with reqar ,-i to their ability to of r i'- i !-. - : . , . .
Twin wap ;,-''. i
conclusion n,;. .
to the re1 <= 'it < ' ~ . < i , ->
r eten t ion >i pr.< ; ' ., , ,
T s a hyp'i I ' ir.'i' ' , ; i
the hypol imn i 01., rt
not the on 1 y 'n,, KM > ,-
t e.-.i. . ; ; >' '^<-- <-! <
anae: oh. ~- ->V- < ;
phOSJ'ho: !' ' l"! -- ' , -. ' ';«*
Ver y f'XU^l1'- i .-.- . ,
J It t.<:r a : ,i! "n - ' ,
mo s e ' i f f i ', i * *
at v:ii iw.T > -' :
dl urn ,<;';
s inoo !,p-r ' ^ ' -'
« Jo<; 1 1 nr.<-
hi--.*- i , ,
alijm may n >' l>v- ; if ' > -
The J i *" total .-^rpa -
where an ac'-,ir r ': t. '
allow "'5iT( ^ :.. ; .I,!..,-
phOSpllOl 'IS f-> fl<-'' Hit "'it ; M.i: :
Effect in 0< induct ci'i' > , ;ni, A'< ,'>-,
chem i '.
-------
vs'ith col if or in
Presumably
c'ii3 .c: u face, in
'? 1C1 the lakes
exceeded
, ', in 1972 was
iiq East Twin's
i the summer of
;< k-)=--!, 2G (3
' ,! t f>r i.nq West
! «--,;t of septic
^'al c'oliforms
; '. n° water
U-0 ml) .
- o.)! ; was
. i j riev5 loped
-'i r <-j;f''ii.at ive of
w! "*er \ hi oh
-: i ; i "< ; about a
; t !« i;-.pr i nq and
* i - mp'-j'.-t of
.!..!, (COJ '-5
- .nterva.ts
' i ; por t dat a
-------
-------
25
20
15
10
5
0
10
5
0
15
*0
15
10
5
0
10
5
SURFACE (0.1 M) CELL VOLUME
-WEST TWIN
*EAST TWIN
1971
1972
1973
1974
1976
MAY JUN JUL AUG SEP OCT
FIGURE 22. Changes in summer surface ce]1 volume of the Twin LaKes 1971-1976
64
-------
volumes of both lakes have remained at about 5 yl/1, a value expected of mod-
erately eutrophic lakes (Vollenweider , 1968),
In 1976, the year after alum treatment, spring ..-en vol'im3? were very
d i i f ej ent . West Twin was clear and had no blue-qree<< >iqr>", whc-ri-as East Twin
was a greenish-brown color and supported a dens" t loom of Oscillator la
L'r1^£§-(r^iis T^)e same pattern occurred in spring 1^77. By summer 1976 both
lakes had a smaller cell volume than had occur i<-d in any pluvious /eai , except
1973. Since algicide use was small in 1976, it appears that the alum
application, which resulted in a lower epi Limnetic total phosphorus but not
SRP concentration, combined with the lowet phosphor a-; im-orm- >?~ J976, was
effective in lower inq cell volume. It is suggested fhat t- n< absence of a
sprinu hi 10 -cjr f'f» ri a : -i t bloom in West Twin may also !>< olue-green alga^ blooms .tppaif-cr iy -r iqinato fr.on
pooulat :ons in the r><>" mne'its (Reynolds and Walsby, 1976),
" " ~ M '' " f-r ri '' .lanqes !: s,u f.n -> . r i. ,t ; i - .- , . --.»-;
pai a lit--, eu ceil vuJ um<-> changes . Chlorophyll in Wo^t Twin iij r .r r ^ , .f is-;i betweeri
spring total phospfior ur t'onoen'"?" -jt / >n and n*'.»-i : i ',.- ;.;, ' if; |-T « '> ; ,
phyll >!" '.-;-14r' ;r ,:!- -./M" . The"-^ 1'ikes
. :;!'-- in the species composition ot the summer sur fa<"" phytoplankton
1 o i J owed -> s im i lot pattern each year . An »"> >.' i .' --pi i nu .1 a'oir bloom
it'liSiL1 ^ ^-Lid' Asterjor.el la'' W'1S followed b> a si at f . i >< ; 1 volume in
Lite Apt i 1 early May, and t-h«n a series >f M'H- or > ''';"> b" (>:rr- ic-''irre'1
ovf*r i ?, sumni" , «ci' t. di '.torn:" .is sub-domi p =i<'* '>..; ; ];)tJ ,-\ ? ,;.,; , , M?
jAnabaj- n a ximnetjcd <-t Ajjhaniv'oniei.Kjri ^fl^JSj a^uae, .ind i.r i - pi- - ,.. .1
November . The summer dominant in both lakes in all /e-.-11'- .->-;' 4 ,i c1 :'^,'5
waf> ^' £los~ac[uae. A. limnetica was the 1974-7'j d. !;, n-i.if , ; tioth la^es.
In 1974 and 19"7",., Ohlorophyta and Dinophyceae began to be a more abundant
component ,;f the late summer algae (Table 22), In 1976, the year after alurr
t > eatmen1-, i blue-green algae dominance was qreaMy reduced, particularly in
Kast Twin, the downstream control lake,
Tr>- seston content of West Twin's su' f ac^ waters ,VT-I -,< , -o;, , "iQ11
* '' as w'. ' ' * ' : ' - ' ' ' >[ y 1 f ':>.- I i n< '> 7 - ,'''
Level tiito'igh l'-)J'-> c. 1.4.;''-' --4% .
seston, and chlorophyll i,rigur.* 2' . Ir> !'y) t) nrnparency of W^^t Twin exce--l<-'J i rn*=>t.<:M
while East Twin remained murky due to Osc_il lator ia. In 1976 ';!,<-' int<;ival of
high water clariry i > w^st Twin pfM"isted i m !;','. 'Hi>- ,;ddsurruTit-t tran-.-
parency has remained at about 2 meters following an initial inciease between
' '" ' ! and 1972 foi Wes* Twin, a l°vral fonnd in m<.">ii°j ate ly <=>ut>'>pi ' lak"f",
-------
80
60
40
20
20
0
^20
> 0
I 40
O
0,20
0
60
40
20
0
20
FIGURE 23.
SURFACE (0.1 M) CHLOROPHYLL
WEST TWIN
EAST TWIN
1971
**
A, 1973
1975
1976
MIAY JUN JUL AUG SEP OCT
Changes in summer surface chlorophyll
-------
25
20
15
10
5
0
5
0
o:
c/)
SURFACE C0.1M) SESTON
A f
y *
K|
V.
-'
v
TWIN
TWIN
1971
* 1 Q 7 *5
, -. i zy i *j
1976
g
-J5
lo
10
5
0
MAY J U f-,' , j i J L A U G S F P O C T
FIGURE 24, "hr-\nu<-»; !- ---.rp;. .- - ;>' ^,-,' >., . , *»,,. .v ,, . ,^;PJ ' ' ' iT't,
-------
6
4
2
0
4
2
0
4
2
CO
LU
h-
LU 4
4
2
0
TRANSPARENCY
'WEST TWIN
» -EAST TWIN
1971
1972
tt- - < «
1974
Or
1975
1976
MAY JUN JUL AUG SEP OCT
FIGURE 25. Changes in summer transparency of Hie Twin Lakes, 1971-1976
68
-------
T.lhJe ?.-', MKAN
-------
','IR H w'.j - P patter ri of ciMP'je: in I h^ oxygen deficits (Table 23) which
roiii.] i.. elat--.j to septic: tank d ivor.- J >n or to the alum treatment.
T-.;-'-.! i, ,1 : :: .>-.,. oy :;'-*v,,jri. (i TA i tor K.i'xp- MenrJot a, the deficits were
h:. >s;» i -<! , - ' - * e : /, i >; >iay of t -,. -o:;1 (r = . ;'97| ,. suggesting that the
oxyqt^i ! f ! : !) . ,-j-. : , .-TO- t'i'-y ,M.> i.-ut i oph Lc, i:- not directly related
t o pr! *< it.1 ' i v i' y
T, [.;..- ,'1. f)\L'.i.N i Kr' i! ' iTS (»»' FAST AN!) WEHT TWIN
LAKK-; ri"i > > M M' -i,t ii
V-:' 1'WJN
. j-'t.yt t-r ,vr- r.u've/ed by Rogers
f a\ i ;"-: I ,' --tt«r tdot. These plants
; i w'if I=>-~ L> -j M!'.{..a i eriijy, high
j'i. '-'j,s. The Carlson
- p 'w;f«q sea;i-.;n (May 1
j| .-..((.; depth (SD) ,
,i 1 uhosphorus (TP) ,
. , i .); e-dj version TS I
'' '; ! tot 1969. Averages
>i. ,ir" teported in Table
-------
-------
The TSI for East Twin did not vary much trorr one year to lh~- ne*t, and for
the years 19(59 to 1975 the same can b<- .'id .if We-.t I'win, witn the exception of
1973 determinations. In 1973 the 1-.I -Ujtermi nat ion trom Seech i depth an-i from
chlorophyll a observations are sut>- __.., '.ally l^w^r tnan other
1973 TSI determined from total ph us i c. net ,11 f t-< :it .;-'-, i
suggests that the phytoplankton c-f r 'ty W.JH im'"-! b/ ivi,.
than phosphorus, prooably a very ht s addition <>i hoi !!'. i i'. ,
TSI determined from each set of obs*.-- .-.tion.-j \r\ !9/(, w.j L-w^t
years. Although this decrease is r,. t statist ically :-iqri:. f
analysis of variance) it does suggest that the app i j ^at i"i. -3
has had some impact on the degree oi eutfophy. iriib vj'-w - '
reduction in cell volume and the change in a i 3-1 i '.-.>-> !-; I'l.ji;;,,
-------
Shi "['I UN 7
DISCUSSION
The result, s of. this study have imp] ic.i' i >;. if lake nuin-> ,t-, foi lake
ei ass i f icat ion and for general under stand ing t t trie 'Hit roph i '.-at i ;n protlem in
s iii-i 1 1 1 akes .
Meptu; tank systems have been commonly ; nrM i le>i in reside-'* ;al leveiop-
--f)h;rui -> ' ' noi intei iakes vi.i qt CM, i iw }« ' r -i !iig> ^rr.'iO:' because or
r,-<-' .-"jptw- oapacits ot s;il--. As ---jfl..! ; '-I'f.-i .-;'. . y !HKiir-y and
:-t .'-'puc ns- M. i!9' ',} , ol < sy;ten!S r-i t.iose wi*:,1 JIPJ- t-'etoh^l v :*: ; tables in
r "' ' ii iv ~ .. ; :irr, ! - nxpt'C'te-d t > (. i1, j-,, ir.,,;r. K, r'- > ,« *v S''f wat-'T. Tin": ex-1'1 inae.1 w.i'i « :-'V>ITI(- *-,, t(>f '";e] i * r oni th"
'.'r< "^ ! ; t ft i , -r ct- vVcitef and tr-i'ri.n.t , 'u jr i.a^' ,- ,c "i >, ; ; s tr.f
ai'i.nq in ban ari-as pi ')'
'T'l.-- 'iiversioii .->{ the septic tanK sy;>te'i, a.ion'j end >< ' -e'v-lt jn a
reduction of phosphf ri us income to the Vol. 1 enwo idei (I97t) "af- .>;>! able" level.
['his war oorif timed h^ levels of algal standing r >( ' we y^a; - ,-'-t-i diversion
j;.J by a TjophiO Stat« index (Catl-,on, 19"7},
-. ! , r -1' f i , ir.d congest.i< t;. How",>.,-< r , cf.--i-in ,.-md s'.reet wastes as w-j | ,j:,
,v, : ,. ;; , .' :\- ' the lak--> tnd n^t i. ;
'- ; ;.t w r JaK- . t1;,!' c(o not provide the ; jn.p! . ? C ,'-,',-
L-;ioiifd ri/ >-:t her *-he developers or the i >..,<-- ,-n -c ,,
')': 1 !<( ' ai '-; whi'-1, t^ceive point v.ou' ces ,-f -, c r i. '> , : : S-.ikef- ' "i/;'
i'^come culturally eutrophic from diffuse sour>^s, be yel^pnie. f continues or,
! h^ wa1-' r -'.er]f IP mar a «d, a marsh filled, or wher - son:' -t ne- >peration i .-
pouifed which has a large impact on the lik -. '''<"^ i^u-.! development
73
-------
practice is to leave the cleared land without cover for a year or more during
home construction, thus adding tons of soil to the lake. As a result of years
of these practices, the littoral zone has expanded from erosion, creating a
favorable environment for the major nuisance, macrophytes.
It is not likely that this very common type of eutrophicatiori problem
will be solved by reducing the income of nutrients alone through septic tank
diversion. A rigorous land use policy and storm water diversion might slow
the further deterioration of the lakes, but these steps are expensive and
politically unpopular, and in some cases impossible if the land owner has the
deeded right to develop the land, regardless of its suitability for such
development. Even if phosphorus income can be greatly reduced, this may not
alter the macrophyte problem and tnese plants and their associated biota may
continue to add phosphorus to the epilimnion at rates sufficient to support
algae growth, even after further nutrient diversion,.
The prognosis for the Twin La
-------
that which might, have neen
satisfactor ily control led,
spring Concent t..;h :.^>. - - "in a >
>r;e r h- ' . n:.
results of rhi -' ;At-i<
internal pho^r-h'ji , S ;-ii
f qt oundwa I "t ';;';, ;
: i ^Sf-3 thr i -i'.t t 'i'~ ; , t-
phosph'. -. u. .
rej-ased from hypolimnetic muds, appears to be
'I'hir. may lead to smaller summer algal blooms if
"' i ->i; ' .t 'in t h' '>. ; no upoii f h*"1
.!, «, i i . '.-> ii?'M)i:ify .31: ( 'j'sant > f_- ' .V? sources !>f
' '. r'iii tin lit)-.vt.al, and to a,',1'^-';-.. i ii'- .signif ica^-ci.'
M .'i. >t'K; int.' t |K> water '-? ' h<> lit* '3! xtjne as it
'' .;); ;rfMit , The next a him application should be
:ii a tea >f -i small lake i or. which hherf is a good
The pr.-f.r- ',' < ---..
algal proble'tis, ,-^,'J i
the most si qni t > canr-
tion due to aesr ,h-jM <- ,
significance i ,-.*'
In many of '.'.-
eastern jId" <
problem. Th i'
li*-tor al T-V. -
-ic; f icien;. ."
signifiean' -i
rorh '<-at; .in h^s h,»an i, ' octed toward
'trcctly idcMittf'ii ! this nuisance as
: -ularly thont whi-h deserve protec-
MII^I < i a I roar-.'jMs, How-i-'-'i , of equal
- ' .' r .' s"! .. ; T' .=- 1 ..': it vfj' 'i !'*-> !-;'% they nia
;'- ^ i 1 1 q ' 1 r
imports:.'.
r^.Tuct i v^
t t at ion - -liqai biomass
i(.!|t« havp> observed that
; - j... , i ,. tt-,1. -[-hi -
pr ed i ,r."c
phor'js :;-- .
both ; i' ; . ,
alqal Slo.\:, ; st
income through d
of the internal
: i i .-.' i '. .'. .r i' , i' ' , i" i i . i >t"
not only a reduction in natrient
'-; , biit land inanaqerfien'; and control
-------
REFERENCES
1. Algal Assay Procedure Bottle Test. 1971. National Eutrophication
Research Program. Environmental Protection Agency.
2. American Public Health Association. 1965. Standard Methods for the
Examination of Water and Wastewater. 12th Edition. APHA,, Inc., New
York.
3. Anonymous. 1970. Aluminum Sulfate. Allied Chemical Corp., Industrial
Chemicals Division, Morristown, N.J. Technical Bulletin.
4. Brown, R.C. 1885. History of Portage County. Warner, Beers, and Co.,
Chicago.
5. Buller, R. 1974. The chemical geohydroloqy of Twin Lakes, Ohio. M.S.
Thesis,, Kent State University.
6. Carlson, R.E. 1977. A trophic state index for lakes. Limnol.
Oceanogr. 22: 361-369.
7. Chiaudani, G. and M. Vighi, 1974. The N:P ratio and tests with
Selenastrum to predict eutrophication in lakes, Wat. Res. 8:1063-1069.
8. Cooke, G.D. 1973. Discussion. _IN: Modeling _the Eutrophication
Process. E.J. Middlebrooks, D.H. Falkenb-jrg, and T.E. Maloney (Eds.).
Utah Water Research Laboratory, pp. 211.
9. , T. N. Bhargava, M.R. McComas, M.C. Wilson, and R.T. Heath. 1973.
Some aspects of phosphorus dynamics of the Twin Lakes Watershed. In;
Modeling the Eutrohpicatior. Process. E.J. Middlebrooks, D.H.
Falkenborg, and T.E. Maloney (Eds.). Utah Water Research Laboratory.
pp. 57-72.
10. ,, and M.R. McComas. 1974. Geological, hydrolog ical, and limnol-
ogical description of the Twin Lakes Watershed. North American Project
Report.. USEPA, Corvallis, Oregon.
11. ,, D.R. Waller, R. McComas, and R.T. Heath. 1975, Limno Log ical and
ge-ochernical cnaracter istics of the Twin Lanes Watershed, O'lio, USA,
1972-1974. North American Project Report. USEPA, Corvallis, Oregon.
76
-------
12. ______ , M,R. McComas, n.W. Wall0!, an-i t?,n, KPI, ,,=-,n
occin r .--T.CP of : n*-e>r na 1 phosph'ir i" ! H'io ;- * '
gla<"i,i! 1-IK'-'- HI ?i--t'"f '^s , M'i. . ;, i.
J 3. Di 1 Lori, f\ : ,, . |. ,. :<, 3;,,- M ' , ,
^ p ] ,q t" ? ' jp, J' I ' " ' , *- I v;,j - I ). - , - i
14. , It ' '" ("!,'! -I"-; ' ,1 f i ir ; : !--->, r..w i^f-. ! '
1 778.
17. F(Jnvr,'i< -..
t.o>- --) t r < t > '
18, V\ f" !"* rt'
in ,v i'- - ; >
r j \ '}'':,- ' ' -
19 . Fe r > i -- . : ,
of tq;! if^: *
am : ,-
1,7
2 I . Kt rnk , ' . - in l , in- '
phosphor is eompou'i'ls i r', la
22. Heath, R, rr an'-" :,!'. ''O,
phosphat -i -*' )' "» .-:f-jfipi
25. He i ;.t ,.,:,. l
-------
26. Kennedy,. R.H. 1978. Nutrient inactivation with aluminum sulfate as a
.. Kent State University.
* H:?.S method of estimating
---. Hf<--, 11:182-183.
i - -.' !->": of marine algae.
its os of carp as a major
Vf>:h. tnt. Ver. Limnol.
.vional distrlbjtion of
, Pot t oqe County, Ohio.
-'V*. Heinu.'di of phosphates
, . I- I - ' /
uiKlwft f-r entering Lake
, ,r i ;> na>"->t a ,
y from three different
s, M.S. Thesis. Kent
A '/unt i rat. ive comparison of pigment
: ;;ier f 3 11 n r s. Ti;rno], Oceangr
[>>;-)' topi anKton concen-
McHoy, C.P., R.'.'. Barsaar.e, and M.NeDert. 1.972. Phosphorus cycling in
an eelgrass (ZO£tera mar i_n_a L. } ecosystem. Limnol. Oceanogr . 17:58-67.
>. '( . ' ',(<"!,, , i i ; . ,;"», if. 1^74. A]q-:il pi oduciiivity in
;s-,:a- - , w'at.Kes. 8:667-679.
-', i > i , ' f ' ;"'Jippnf s and water in
i.1 : ' >'..i') !-> requlatory mechanisms.
Acta
,, >'" from storm rainfall.
Chdp, 10, 1971
-------
of * tu- ri r t . ,] , Wat"
-------
55. Stauf f er , R.E., and G.F. Lee. 1973. The role of thermocLine migration
in regulating algal blooms. Cn: Mcdeli_py_ tbc Eu< rophieot !;! F '<-<.<*.-
E.J. Middlebrooks, D.H. Falkenborq, and T.FI. Maion^v 'I-T;.. ! , i, w, ,-,---.,
Research Laboratory, pp. 73-82.
56. Stewart, K.S. 1976. Oxygen deficit;-,, (I a;'., .n ' - - 1 , -
Madison lakes. Int. Rev. ger, . Hydrot - , : !,
57. Strickland, J.D..H. and T.P. Parsons. I^b8. A Manned o_f riej Wat-M
Analysis. Bull. No. 125 (3rd. Edit.}. Fisheries Research Board, (Vin^n.-.
Ottawa.
58. Stumm, W. 1964. Discussion. P. .;*--'.'.'.
Pollution Research Proc. 1st Int. Conf. W !*>;,
Ltd., London, Vol. 2.
59. Szczepar- WSK i , ?.- ;9<'6 A.-pt/cts - : i -. iv\, : ; ] . -w P-, i-.^ '!
merits, Kast Twin I,ak--» t'orLage County, orn.-. M.S. Theses, Ke-it State
U.i J ver si ty .
60. U.S. Enviro^'T.e.. :al Protection Ag-u- y !'»7l. Methods for Chemical
Analysis of Wdtf-r v-, 1 Wastes. Nat-'l D:I/. !.>--, ;,'t/., Cincinnati.
61. Vollenweider, P.A. I46H. " -»juific' : ;inu.i,,*-,i i; : >.T T h.? eut r< >phi ';at ion
of lakes and flowing watf-r;-. .< -' par' i'-'j' M r f-fpr <--j,re. to ohospiir^UK arvi
nitrogen as factors \>.i . ! . , .'>''' ' Vcnnica1 !<«-(.'u *
DAS/CSI/68.27.
62. , 1976. Advances in defining
phorus in lake eutropnication. Mom.
63. , and P.,I. Dillon.
__
loading concept to eutrophicat ion te.- --it . N-- '
Burlington, Ontario.
64. Waller, D.W., G.D. Cooke, M.R. McComas, and R.T. Heath. 1976.
Limnological and geochemical characteristics of the -Twin Lakes Water-
shed, Ohio. U.S.A. 1972-1976. North American Project Report. liSKPf ,
Corvallis, Oregon.
65. Wilbur, D.L. 1974. The effect of aluminum sulfate application f >r
eutrophic lake restoration on benthic nacroinvort^hrates i;v( i
Northern Fathead Minnow (Pirnepriaies urome^las Ha!.1 f»-.:T. The:;; , ': : i
State University.
66. Winslow, J.D. and G.W, White. I06b. Oe '
of Portage Co., Ohio. USGS Prof. Pap. 511.
80
-------
APPENDIX
INTRODUCTION
A general outline of our approach to aluminum sulfate dose determination,
experiments to test its effectiveness, and application procedures was given in
the Materials and Methods section. Here the step-by-step approach taken
during this investigation is described in detail. Experiments were confined
a* fir-t to the laboratory, then to _in sjtu enclosures to test toxicity and
-. »t»-<-t i/en<">ss, and finally to a pilot lake treatment (Dollar Lake). It was
i < ' i'-vi T n-it if, at any step, there w>< - ev; i-'-M- of t-l,t> ;-<,-. j h \ 1 j ty o>"
iaflui \ i -; side effects then no fu! l-scM-!f lak'1 ;; -'a* ;'!en*. WM'J occur. The
successful treatment of the eutrophic Dollar Lake (1974) was the final step
before treatment of West Twin in 1975. A further description of these
experiments, including a complete desor ipt ion ,if )i< ')-!ia; '.ru- treatment, is
given i;. Wilbur il^'M' and Kennedy <197!';.
T'u A.ppe,. j i x is organized to give the i-e^-;- r a .summary ot the experi-
ments T: ' procedure foi the detei minat ion of West Twin's dose is given in
;-' ' I-ina ;!'/, a section is presented on the equipment arui application
d^si.^n, the application procedure for the West Twin treatment, and a summary
of costs. Non-metric units are used in portions of the Appendix since
aluminum sulfate is supplied as gallons or pounds ind temper nt-ur e and other
correct sons are based on these units.
DOSE DETERMINATION EXPERIMENT
LdKe waters collected at varying depths (and thus witn .r", i-,q total
alkalinity) in West 'IVin Lake and Dollar Lake were -re-ii.ed -»ith aluminun
sulfate at dosages ranging from 0-50 mg Al/1 to confirm the relationship
between the amount of aluminum added and initial alkalinity. One liter jars
containJna 500 ml of lake water were stirred at 40 RPM f~>r two minutes
following the addition of a liquid concentrate of aluminum sulfate. Changes
in pH wet^ measured during the first two minutes. Supernatants were sub-
ampl^d following a 12 to 24 hour settling ppi i od and m<--> i iur ^ment.s of
alkalinity arid dissolved aluminum taken.
Results obr.ained frc-.T "Lc *r "fitment of We'-^ Twin Lake ' rac't^r ^at'-r
(initial total alkalinity - 137,3 rru ;--"Oj-'l) ate typical 'Figure A-li .
Doses of 1 fo 26 mg Al/1 produced a larue. set 11 f^l- \ <-> floe, while doses ah-ove 26.
mq Al/1 resulted in a white turbid inaction mixture which did not settle affer
18 hours. No measurable floe was produced at dosages below 1 ;ng Al, i.
Alkalinity dropped rapidly between 0.5 and 26 mg Al/1 (117.3 t o. 0 my -"aCOa
/I.) and war, completely removed above a dose of 30 mg A!<1. pF wris reduced from
".2 to S.li at 26 mg A] . 1 and to 4.9 at 3D mg Al/1.
81
-------
o
w
Total Alkalinity (mgCaCOj/L)
80 o o
08 O «
O
i
4J
82
-------
Residual dissol/>>.i dl'inirni'r, high in the dose range 1 to 7 mg Al/1,
remained low (.02 my r>'. '!.) ir the !(>.> tange 9 to 23 mg Al/1. Doses above 24
mg Al/1 resulted it) ol^-vare'; rA~j;iuai dissolved aluminum concentrations. The
maximum dose for thi ^ '* J ka 1 i H it> Wc\ = calculated to be 24.2 mg Al/1 since this.
dosage represents the .''.ixi^'in amount -jf al'jminum which can he added (under the'
conditions of this *«,~t, i.->., / -pi"ut-° mixing) before residual dissolved
aluminum concentration ex<-°'-dci, 0,0; FV.I Al.-1, a lev<='1 i epor ted t<> be toleratec
by trout (Ever bar t n.d ' i ->-, if. ' ^ " ., ,
Maxim, ifti dos-jc;* ^ ~i I.-:,: um- i - IIK*- m.anner for the full range of
alkalinities ! A.r.d : ; ; e^f- i V . :} *o d«t >-r ": ne th*' relationship'
between alkalinity ar'i a lunur.up: do-»> .i-nnq linear £ egr f"r; i on techniques. Th«
relationship is expr-"
Where:
The slope of this !ir- war - that bar.-d on stoirh sometr y and wac.
found not to be si-^r,: * !'"c-i!it ! / :. ! f *>r »rit ('f- .OS). The I iw int-'-r cept value,
as yet jnexplained, " ;:j^'-t ; M;^ -.. ^",s;t , f'.r t).-- £ or (ring such *ests prior t',
any lake treatment fc L .- , ' i »,- - !.-!. -jir.,.- ! ve.' -il iminum values and to
avoid unne^ess-M i./ « pH :' ; > "i pr-1'-- i'i'i-- *' -i>- f-, j lowed in * ho
calculat s >' )' -f . X -r ' - - -;-.- i- -.,-' f f;, ;i. , ~ . -,,, ,
doses -: '- 'if';! - t / . : i .;-'- > -,,..<;
water. co [.»'; ' r - . r :-,'-- -
in *-;.» ia>- -'. , ' - . - . i - -t ~ -if, ' ( , i "''"<
alkalinity ->.:.. , : - . > ' ' - ""; 11 i;i i ' af- -*',
jsel t-, d-' - ,i r- . , , " ,; '
Pnospn jr. a- !' ' ' ' -,.i v i i ,'i' - i 'i',. t i :ici1' i. .: iaK'j wa* ''jr
spiked 'A i t , :.',< H -.-' i , : , . i .-,. -ri'- 'Ton-..: ' ; . ITT, ; . a
P/l to i 15 : ,.-; J " i : - . i4 !',.) Ai i, ;!,<^ wax t TI in iu-'p :->r v.,d f
wi f h an a L '-. < i i ; , '.',', ' t - : v ' 1 1> v ; ng '-.^t t 1 ing - f i '.3 ' t, i- ,-
phosphorus con.'entra; '< n^ r^il,i^.i i; tin i "> t.-> ^2 ;:; ij ' ) jndLoa* < rui tliat j^if ;
cient removal ?''ull l - a<^h (- ", r-.i
commonly exp"i" ienc'-' ; ' " (,« < ','JK,-
,-.!-), . .T .. , - .,; - .,, , ^ i . i
A s-c; r d --:. -- , ,',-' : ' - v-'
retention " ipo' : - .' ! . / 'i .,!- f; c v -i -a; ; ; ;-: p^r ) .11 ( .
retarding .'-i>' ';/> r . i ; ; ,f.'r., . , * . , wcf*-.(-r ,nt. .
face. FOu" -1 i' :; ' i ... , ,:,. -' ] < ,- - . ', <> T t 11,'J.---
The barrel- ; .,. . ., ^ , ,<>', : ..) -.. :, ...K..>-! w > .
glass wool to pt <-,- < , j ... :, ->...,,. M.-. .> , r»(/Pi /f>,j
known quantity ,r \-.\-- ' > »* ' *',,';< r oni 9.-iri',! ;;
to 8.959 mg. Tt.*- ^ - - . '-.^ r- "nt-iiu- < ,!-
-------
n3
i_i
Q)
\
(U
D
-U
-------
col urn a was capped and fitted with un v and <,itf!ow port,- ,it,d rioted
rate of 8.31 ml/h with a phosphorus so1. ,'i\ conraininq 10 mq .''!. l'h» }.
the three experimental columns was ma < > >f-d at pH f>, ' hi ricK>-t
pH values which miqht h^ found at *- wi
collected at 100 ml j'.-^-rvals f->r fn.o,.
phosphorus lost to t h" columnr wa° '-a I "d
The max Lmurr phosphorus reinovil -tj.
conditions of t h>a t^st, was r pat h"d it A!
and ) . 3 1 ] , r ^Sfi^ . H ^" , ',:; ^^ n- ; <, ;
from the v;i Unnri'r ,
This r-xp0!, IiTCTSt ptOV'id^'d f .Jt f!if-r PV
dosage should h'- t-.,i ,i- i :p-.n w,it--r ^ J < ;i ,
content -s ne L^kr., 1'';^, -,; j,- t t .
release frr>ri ! <>, " ">' i i,f :t^. '((> <
requires the larqe::t ainoutit if ,-t i i,in i p'lni ;
upper limit haFsed ->n KUA, The effect i <- .-
of the sediment r, . Dn*- ,- . <; [. tc IT (<-,--; ,..^t; i -
tial water pH catinot :»< .51 ; : ,1 ,: ;< .' . <
than in <-h»- .jpt- - : ' it ,* -:
IN srru cif.i ';MN f-x' ';> MI :-.
int . t t iiu > i
-------
nreri uurjrig the first
';>!Mt:J 'f. osr 68- ig P/] to 7 JJ g
M.--:n-,i:ir reaction in total
i ' '..juto at*'FT treatment, at
'- < ; 5 j g P/ J. and 4 3
.. --I;'1 'it'.ons a: 5 and 7
wi -j ,~,Hia 1 reduction in
0! "oi.ti r,uf>d .^ediraenta-
lo^,i! (- t-.y SCUBA
:j -in i i «.- la/er
; ,. in'\ fiad no
1 (-,: t f t W^f-n 7 M
v ' '.not it i.i' appiica
> - n:ii''>nt ohosphorus
; r,,,.'-' >nc'F-nt: at ion at
'.la/ ».- to 340 yg
. i ! '', us ! oC'-'-ntration
' ... < t J.'j u.j P/l
; - ..M ! -' .'jut c:e ot
1 - i - } r ,3 . *- in
i i, i r; >-- ex--
1' ^ct i ve 111
i.. ' ' < I ' >w i n q
; i; : f'~!>ve t -
i r: ,11 ' ev-I,- /
; . :; j ;.>H ' s.
' I.'H Al/i ,
A <--: -1 Tw i n
-------
p. i! t ,.i i ' .j ,...,..' ,1 ; -, -, < " f ,,: : .'. in ,i--i\f\' I -.
ma int a irif-i if f.H 4 . (-> w . t n <'. -,.;. o , -, ',',.',, ., , . u , IM > !.' i ;>-) A ', , i T it i <= A- i , a P.'
UJUP. i' H>C! ! i he :--|T'-': ti. (>'': 'r - i Tifjn:? . l-'J^.
i: iii '\ i !, T 4-i-;pf,( - i'. o j-j i , \]\'i'i i -:' t.) v/,itf-rr% ma i nt a i rieri at
<{ it'')' 'i.iw: ! p'i 4 , () ,T!i-! ;f!'et\/inq I \<
-,-: i > "'j,' -) )!». M.iSK-i < f hf ; ^rj_>OM-«-
f , . - ii, 'i . t -ii <- , wl ., t, !., ,),- dPt in i !- i- -"
n. "i ' i' 'f ' f-'j'Mi 'i ii L'">c?-" than ,).(1S IIHJ
-------
this case, two sampling dates. If the two have no species in common, both CC
and PS will equal zero. The maximum value of CC (i.e., 100) occurs when both
samples have identical species lists, and the maximum value of PS (i.e., 100;
occurs if both samples have the same species in the same proportions (Vielou,
1975). Results of these analyses suggest that the application of aluminum
sulfate, or its accompanying side-effects (high sulfate concent r-->, -.Lou;, and
low pH) , does not seriously effect macrobenthLc organisms or maciobentnic
community structure,, With the exception of the but fered-alum treatment
enclosures, all enclosures experienced a similar decrease in nurnb^i~ o;
organisms during the interval day one to day fourteen (Tablo A-2;. All ^f t h=,j
enclosures showed little change in total number of specie!:; (Table A-2)
Comparisons of diversity (similarity) indices indicated a hj ;:4
Table A-3. DIVERSITY INDEX VALUES COMPARING
SAMPLING DATES OF EACH GROUP
Group
A
B
C
D
CC
55
63
68
53
PS;-
69
c.6
74
/ *
From Wilbur 1974
-------
IX'LLAR LAKE TREATMENT
The results of these experiments with effectiveness and toxicity led to a
pilot lake treatment.
1. S M) eut
July 1974
pr incMpal
treatment.
>?f feet i Mt-.
Dollar lake, a small (2.2 ha), dimictic, shallow (Z
Dphic lake north of East Twin was given a hypolimnetic treatment in
The complete results are described in Kennedy (1978). Two
)bservations were made which formed the basis foi the West Twin
First, no toxicity to fish was seen. Secondly, thy alum was very
in removing phosphorus from the water column and in retarding
from the sediments.
An experiment wa.-: conducted to measure phosphoi us release l rom treated
an>1 intr e/i r eii ^e-i imetif s. Plastic wastebank^ts, fitted with sampling pot tp to
wli'i'ti -. plastic baq -ould be attached, were inverted and placed in hypo-
1 imne1 sc n:-i<}^. nefore treatment. After treatment additional baskets were
invf-rt^d ovf>r: t loc-'Covered sediments next to trie control basK^ts. Samples
w^'f * ikfv over a period of one week in 1974 and 1976 and the water analyzed
for tot-a) phosphorus. Treated mud? (Table A-4) released very small amounts of
phosp'i'"-;is , par t i culat 1 y in 1974, further substantiating the conclusions from
'ho in ,it;i columns that alum-treated anoxic s>-dimfjnts hav^ '.-jw phosphor ;'S
-'Kaf-'^ raten, and the concljsions that continued ir ternal phospt-'Orus loading
i'i West Twu> a't'-r ^t^itment must t-ome in t^rt fr--.:i -i source >'M !-f thin ancx1, .:
'i ,'u< 11 rr.ne! :' sf-Jimer;' .,
Tdihip A-4,. TOTAL PHOSPHORUS CONCENTRATION IN
WATERS FROM TREATED AND UNT^KATFD
ANAEROBIi' FMiLI.AH LAKF. SKD1MKNTS
Oep*-' * -Kt i t -Bar r el'
nM un*~ r eated
4M unrr eated
4M tieat ed
JM in' r '*-ated
? 11
19 ft
I 9 7 6
M 9 p<*
[02]
224
i'r ,n,-,i r a' o' ; t ^ t h*-- treatment of West 'Ivvin Lak--, a set ie^ ' ; ii -.-; ! . «i
'id.ict^d 'r->nu; water collected at S, 7, 9 and 11 M. to conf :: the relation-
- : f.etw".1;! ,1 i Ka 1 i ri! t y and dosag^. T!edt:n»'iM wr-- tc. !< -fined t.~. r >.
iv. i -1 i nm i "t> ; !> M and below! .
89
-------
As before, 500 ml subsamples of lake water from a given depth received
increasing amounts of aluminum sulfate, were stirred for 2 minutes, and then
allowed to settle for 24 hours. Each jar in each alkalinity series; was then.
sampled and alkalinity and dissolved aluminum measurements made.
Total alkalinities in mg CaCOj/1 determined immediately prior to alum
addition were:
Total Alkalinity
115.33 mg CaC'0,,/1
137.33
143.93
149.00
With the exception of 7 M water, which received an aluminum dose ranging
from 0.5 mg Al/1 to 26 mg Al/1 all depths received a range of doses intended to
bracket the critical portion of the titration curve. Results of these jar-
tests are given in Table A-5. In each case, dissolved aluminum concentrations
increased exponentially as the critical concentration of 0.05 mg Al/1 was
approached csnd exceeded. Therefore, dissolved aluminum concentrations deter-
mined ait each dose level in each alkalinity series were plotted versus dosage
and fitted with an exponential curve in order to determine the maximum
aluminum dose at each alkalinity:
bx
y = ae
where:
y = dissolved ailuminum concentration (mg Al/1)
x = aluminum dose (mg Al/1)
Values for b and a determined for each data set were:
8.518 x 10 9 0.7875 0.98
9.40 x 10~U 0.8294 0.99
7.121 x 10~15 1.1938 0.96
3.30 x 10~8 0.8401 0.98
90
-------
Table A-5. JAR TEST RESULTS-DISSOLVED ALUMINUM
CONCENTRATION (mq Al/1)
Dosr-
f mg Al-l,
17
meters 11 meters
19
20
21
22
23
24
25
26
27
.0008
!
o
n
0
. UU4U
.0317
.08 SO
. L540
~
(
0
0
0
0
.ouv*
.0286
.0505
.105-
.2050
A dissolved
allowing the c?.'
required at each
Depth
5 M
7 M
9 M
11 M
un ^(-.->;) * cat ion of 0.05 mg AJ/1 was substituted for y
">: .if -, t Le maxirn:im dose of aluminum (in mg Al/1)
Maxim un\_Dp s e
19.791 (mg Aa
. \ , 24.221
' 4 j> < 24,773
149.00 25.167
The apparent- relationship bet ween aJkalinit/ and maximum dosage was
determined by nub ]",-' i r-.y th^sp H;)t i t.-> Mn"ar regression analysis.
y - (J
wher e :
y = aLurniru.rr. !(>,-;
x = initial fr.t.U ilkaiinity (mg CaCO , 1)
-------
This relationship was then used to determine the maximum dose for all
alkalinities within the range 115.33 to 149.0 mg CaCO^/l.
The next step Wcis to determine the dosage to be applied to each one meter
thick strata. The alkalinity of each one meter depth from 5M to 11M was
determined in triplicate, with the mean alkalinity of each one meter interval
(e.g., _> M to 6 M, 6 M to 7 M, etc.) obtained by averaging. Based on :he above
relationship and these average alkalinities, the (volumetric) maximum dose
for each depth interval was calculated. Based on the formula weight of 594.19
(assuming Al2(SOlt)J. 14HZ0) these maximum doses were converted to pounds of
dry alum per cubic meter of lake water by multiplying by O.C2428, the
conversion factor to change mg Al/1 to pounds alum/M^ , as follows:
Depth Interval Average Alkalinity Max. Dose i^-'
5-6 M 121.35 mg CaCo /I 20.907 mg AL/1
6-7 M 132.35 22.9j4
7-bottom 142.91 24.880 0,6041
A dose expressed in terms of pounds ot en y alum per cubic neter was
sufficient to determine the total amount to be added to th^ lake if dry alum
was to be used. However if liquid alum was to r>«- ,:sed, as was the case for the
treatment of West Twin Lake, further calculations were necessary to express
dose in terms of gallons per cubic meter.
The standard strength of commercial alum liquors ranges from 8.0 to 8.5%
Al/Oj , which is equivalent to 5.16 to 5.57 pounds dry alam per gallon (at
60 F). Since liquid alum is shipped at temperatures considerably higher than
60 F, correction must be made to allow for the resulting lower density. For
example, one gallon of 8.5% Al^O^ liquor will contain 5.57 pounds at 103 F.
Alum suppliers provide results of Al/Oj assays with each shipment. It is
important to note that such assays are reported as percent Al,,;;,.3t ,1 standard
temperature of 60° F. The supplier should also be abi« t-_> estimate the
temperature of the liquor at the proposed ti ire ot application by taking
transport and storage time into account. It is advisable that the liquor
temperature be re-checked prior to treatment in case such an estimate is
grossly in error. Knowledge of both temperature and Al^O.i is required in
order to determine dosage in terms of gallons pet cubic meter.
The following procedure was used to determine dosage in terms of gallons
per cubic meter.
1. Percent Al £) i (at 60 F) was converted to density, expressed as
degree Baume (at 60° F) using Figure A-3. The liquor purchased for the West
Twin Lake treatment assayed at 8.3% Al ^ 0 d , or 36.5° Be (60° F) .,
2. A temperature correction was applied against this Baume to account
for the decrease in density using Figure A-4. The estimated temperature of
the liquor at time oE application was 100-105° F (a temperatuie of 103° F
92
-------
CO
-------
2 4 ^
I
2
-
O
o
LJU
O
n ,-\
TEMPERATURE CORRECTIONS
, b >«- ;
Corp. J
.:*'*«tf^iSS!9iS^^
100 120 140 160
! F
-------
was used). The cor t e.'-pondinq cur r e<:r ion racfot i f or 3 <>/' - 36" Be liquors)
-------
o
10
CO
o
CO
CM
0
QG
c
o
'D
0)
Q
LU
I
CO
rtj
.Q
10
q
cd
o
LO
q
CO
|B6/-sq|
96
-------
Treatment quadrats were established by locating east-west transects at
SO M intervals along the original, north-south transact. Coded buoy0 ^rifed
ali i liter sect i ons of oast-west transects with either a not th-sou* h t'tan.^i-' f o>
t h--- perimeter of the treatment zone. Specific quadtat--,, identifiable cy i
Sou,' numbf-M -ode, oo;)i 1 h.'1 easily located by loca'in'j the appropt L-M<- ?. ;;
/-(-.» ]<.-[ buoy T^e c.< s , net locat i'>n of each of the .'<>rnrr buoys was con; I'ir-'-d
MV (- r i ap,'.!>] I -i' i"n ' '.m- "-hot" poiM'-,
Oppf ; >< i,in J ; i iqr- wrt- taken ar each fuioy. The ie readings w^r e i;->i: '
det ei mi ;if t vit> voojm^ ) wafer below ;i depth >f ri M in each quadra' , Volu^'-f. -1
d^[>( h in1'--; >'-i i <" r" i " t -" r ^pt ed by 1-ike boM;-)ii w^re calculated by mul t. ipl v i Mr passef th<"
3f;-h i,;'i -i '< - ii't'.-i i:-dj idti-ill" ', Vilculafing th" v-lumi1 >'f ' '<
t- ,- ' ; '. ' ' I - ',' I !"- ' ' -f I 0V, 1 -P;.ti. ,,f '' Tit^prs w'"t f ''UPlpi. i ,
i' - t ;' K i f < ,, 1 '' i
* ' ", \ t , , t f:>' i 1 kj ; i
i.;h depth iii'-rvdl
\'i ate ur,"d ' 'if < -->a
"-I : . -i] ! '' i >,' I >y qu
' " : - a f rn ^ -;' * f Wf'! ; v :; -^ K w ut diameter. -1 f of. t -It"-^.'
4r .-.)!-.' swi ,,-n :> ,1 with a nu, -; miurp .<;.- -. r , of 7,60(1 gal ! >» wan .' -ed.
I , --f <-..,> i»,, ' WTS ,110 r P t', r; suff !, \f-i,> ,j hold on^ f r K ' ! i ^ ' *
-I,'." -.v , - t ,, ! 4 IJOO qa I 1 ', I ;- ' . ', I it; _,,-.
-------
Table A-6. GALLONS OF ALUMINUM SULFATE APPLIED TO
WEST TWIN LAKE
Quadrat
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
Gallonage
38
234
1436
3077
1866
500
91
11
176
547
627
910
2347
2541
2282
8a5
595
208
181
1654
Quadrat
21
22
23
24
25
26
27
28
29
30
31
32
33
34
35
36
37
38
39
Gallonage
2986
2751
1105
791
927
848
996
554
60
61
380
1220
1070
450
274
430
843
786
211
(2) Delivery system - The delivery system consisted of three components: (1)
a 12 hp, 2 1/2 inch pump, (2) a system of pipe leading from the pool-side pump
out into the lake, and (3) a floating platform, which served as a loading
point for application vehicles.
The pump was located at pool side with the intake port attached to a
siphon laid over the rim of the pool arid the output port attached to the
delivery pipe. Although alum solutions are caustic there appeared to be no
damage to the impeller, casing, or fittings after use. All of these parts
were brass.
98
-------
Tne Piping s y s '. em con s i s ;.
(1/4'' wall) PVC rigid wall pip<-
10 M apart. Two an J one half
pump to i he laKe snore to av'.
pipe terminated at d outtertly
in the laxe and anchor eJ on 3 1 1
fof the .Carrie diame^r), connec'
load in .) '~ inks on apf i !. a c ion >.'
The lor<
a 20 foot sectionr of 2 3/8" I.D.
Jet anchored 55 gabion drums spaced
-_ «d;", licfii for the segment from the
raesented by uneven terrain. The
j on -V tt ' by 8' platform situated
- . A ,1e and lashed with 3 8"
iron. Five rows
';.) drums) for the
stern. Two ,:50
.^ined by 2 1-4"
iliowina a *.>! al
400
weight < 's approximately
500 gallon.-, of alum at
i'..-i miscellaneous on-board
y provide- >,y five and six
. ,-.- '-,;rt ><-; ,m PVC pipe (^
i ; ' M Del ">w each barge by
t -- if »"wo A-* t ames, the I^qs
-; -.- now -jr. J '.he stern. The
.. .'- ^qu--;' ..'i Length f the
; , ..'cippeii --.'. thf? erids, 'and
A I I '/ f'v aasol iae pump,
' r, --. r if- .,-oupling at the
« ;: -'-1 I r orr, j u s t D-- 1 ow t he
.i- f^-.w f r -»ir each source,
'- i i ;i t a iried .-- 50/50 during
"M '.'"',; n>i'.' ' ild. The only
>:pi * itt.ed with work
r '-t ' ' -- controls were
-------
ALUM APPLICATION PROCEDURES
Treatment began on July 29 and required thiee full days to complete. A
total oE 12,693 gallons was added on day one, 12,555 gallons on day two, and
11,671 gallons on the third day. Operations started at approximately 0700 hr
and continued till dark (2200 hr) , giving an. application rate (per barge) of
between 0.26 hr/100 gallons and 0.24 hr/100 gallons. This rate includes time
to load barge tanks and re-position equipment:.,
The platform which received alum ':, cm the shore and served as a "filling
station" for the barges was positioned each day near the quadrats to be
treated, Each platform location allowed the barges to approach from opposite
sides of the platform. To ne loaded, barges were moored, bow in. When the
filling hose was in place end th? line ,-alve opened, instructions to begin
pumping were radioed to the punp operator at pool side. Pumping was
terminated when the tanks were nearly full ind were allowed to completely fill
by gravity flow. When it had been confirmed by radio that the pump was off,
the valve was slowly closed,
Alternately colored floats spaced seven meters apart (the length of the
manifolds) on a 50 meter line served as navigational aids. A line strung
between the north and south buoy at. the eastern end. of the quadrat ard another
line, similarly marked with floats, was strung aJong the western end. The
first float on each line wa.-; 3,5 me tec--; irom the end, with the remaining six
buoys being spaced 7 meters apart. The barqe moved back and forth across the
quadrat by lining-up on lik^-colot f;d ''"lost 5, thus insuring even coverage of
the area. Barge speeds were kep! oelow "t mph. When a quadrat was completed,
the navigational lines and markers wer:-> moved by persons in smaller boats,
while the barges returned for > e-M lling of the tanks,
Surface water and aluir, nuytr 50/-.0, «ere pumped down to the manifold by
an on-board 1 1/2 hp gasoline pump. At rn? erJ of each ran, the pumps were
allowed to pump water only wml^ returrp'ig to the platform to flush out the
steel pump casing.
Equipment dismantling and reiroval required approximately one week.
COST OF WEST TWIN ALUM APPLICATION
The cost of the West Twin treatment is itemized in Table A-7. Labor
costs are not given, but the number of hours spent on construction and
application are listed. The costs for equipment and alum are likely to
increase over the years, but the labor hours could be greatly reduced by the
employment of experienced personnel or by the development of a faster means of
application.
100
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Table A-7, COST FOR THK ALUMINUM SULFATE TREATMENT
,)F WEST TWIN LAKE
A , 1 1 e m i z f ;! ' "> s t s
' . Equipment (re-^sable) $ 4,058
i. , Sup,;,- lies 646
j. Re; ; J!E 262
-5, A 1 ILT j " un sulfate 6,803
TOTA; $11,779
roiii hours, construction
unrj .-ppl ication 2,000
Apr ' - at Ion 590
101
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TECHNICAL REPORT DAI A
}ti i-LRI-OHV:\G ORGANIZATION REPORT NO
! i ." 1 -r PL OF RtF'ORT £,ND PF RIOD COVERED
Final - November 1971-June-19J-
14 SPONSORING AGENCY CODL
br -
ri'jf.s \/ere as--,ed: (1 ) i-Jill septic tank diversion reduce symptoms of eutro-
the "K-.'i'i Lake;, two similar dir.ictic lakes, and (2) Will a maximum hypo-
, residual dissolved aluminum ' O.Ob me,/!) of aluminum sulfate (alum)
'i1 nhospnorus (P) release and further improve them?
.w^ion, P in lakes and streams declined and plankton jiomass declined, bid
of son i tori ^q aftet diversion, D and tiomass remained those of moderate";,}
, a'ld r' inc. "n'1-e re; ained above "permissible". Non-point sources were
ro'-v ,-)r1;! fi-.jfi lesT'-:, maxi °u;'. dose, which is related to alkalinity and
i-'.'1 tests", wa? ofiective in reta>"dinc P release fron sediments. A
r" -,f Dollar Lake in 19/a Was done as a test of the technique. 139.55 M3
' : ; '- ' t°e hyfjo 1 i Miirr ei HesL K-1 NO OF PAGES
2 PRICE
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