Nitrate contamination of groundwater In theRepublic of Lithuania
vALGIRDAS KLlMAS & BERNARDAS PAUKSTYS
Klimas, A. and paukstys, B. 1993: Nitrate contam ination of groun dwater in the Republic of Lithuania. Nor . geol . unoers . Bull. 424. 75-85.
In many countries nitrate contam ination of groundwater has become a serious ecological problemand Lithuania is no exception . In fact , irrational. unbalan ced development of the econom y coupledwith speci fic geolog ical and climatic conditions have led to nitra te contamination on such a scale thatit has become the object of interest for specialists of neighb ouring countr ies.
Contamination is worst in the vicinity of fert ilizer factor ies and intensely manured agriculturalland. Excess ive nitrogen concentrations , typ ically as nitrates . are common in unconfined groundwater which is vulnerable to direct contami nation from the land surface and the atmosphere. Indeeper aquifers , apparentl y relatively iso lated from surface pollution, ammonium is prevalent. Nitrogen contamination of grou ndwater shows a clear increasing tendency with time.
Nitrogen compounds are not necessarily stable. They can be affe cted by various biochem icalreactions. In these react ions . interconversion between nitrates. nitrites and ammonium can occur,as we ll as denitr ificat ion (i.e. loss to the atmosphere as nitrogen gas). Thus, groundwater canpurify itself from such contamination with time.
Algirdas Klimas. ARTVA. Eisiskiu pi. 26, Vilnius. Lithuania. Bernardas Paukstys, State GeologicalService of Lithuania. Konarskio 35. 2600 Vilnius. Lithuan ia.
IntroductionGroundwater is the sole source of drinkingwater in Lithuania (summary map - Fig. 1).This is due to several facto rs; groundwaterresources are very large (Juodkazis 1989,Juodkazis & Klimas 1991), there is abundantavailable recharge (annual precipitation averages from 540 to 930 mm), and geologicalconditions are favourab le (the thickness ofsedimentary rock cover varies from severalhundred metres to two kilometres or more) .
The upper aquifers are composed of glacial(e.g. Samogitian and Baltija Hills, Middle Plain- Fig. 1) and glaciofluvial sands and clays (e.g.Coastal lowland, Southeast Plain). Beneaththese one can also find other fresh groundwater aquifers. It is calculated that potential freshgroundwater resources are around 3.2 millionm'/day in Lithuania (Juodkaz is 1989). Extensive surface water resources (rivers, lakes) alsoexist, but in many places these are pollutedand not suitable for water supply.
During the past 30 years hydrogeologistshave also investigated groundwater quality ,and it is clear that groundwater is threatenedby extens ive pollution (Kondratas & Mikalaus kas 1973, Mikalauskas 1976, Klimas 1979,Klimas 1990). Especially wor rying is the threatposed to groundwater by nitrogen compounds(Zabulis 1988, Klimas 1990a, Klimas 1991),particularly by nitrates. Particular sources of
intens ive nitrogen contamination are industry(e.g. Jonava factory for nitric fert ilizers) andagriculture (e.g. large pig-breed ing farms).
The stud ies of the current, and earlier, authors (Kondratas & Mikalauskas 1973, Klimas& Paukstys 1990, Klimas 1991) show that nitrogen contam ination of groundwater is occurringover pract ically the who le terr itory of lithuania. This phenomenon is largely due to regio nal pollution sources; i.e. atmospheric pollutionand agricultural activity. The effect of the former is not great ; only 5-10 % of groundwatercontam ination may be explained by atmospheric deposition ('acid rain'). The remaining 90-95%is the result of agricultural activity. The prom inence of agricultural pollution is due to several factors. Firstly , during the past 50 years ,an unbalanced agriculture, occupying an areaof some 3.6 million hectares , has been developed. Increased crop-y ields have been achievedalmost purely by the use of mineral fertilizers ,applied by aircraft with little attention beinggiven to the actual requirements of the crops(fertilizers were spread both in autumn/winterand in spring). Typical applications have beenaround 299 kg active fert ilizer per hectare. Ithas also been common practice to spreadmanure on the fields in wintert ime. During thesnowmelt floods , the manure-laden run-off became a source of contamination for surfaceand groundwater alike.
76 Algirdas Klimas & Bernardas Pauk~tys NGU · BULL. 424.1993
N
"
"\............
I(L.,
/-\Dysnaplain
r J L.JLithuanianBielorussian hills
30o 60km,,=,=~=~I
Fig. 1. Location map. show ing the main geom orph ological elements of Lithuania.
itrate cont amination of grou ndwater is asourc e of concern the wor ld over. e.g. in Great'Britain (Foster et al. 1985). Czechoslovakia(Vrba 1985). India (Handa 1983). Republic ofSouth Africa (Heaton et al. 1985). U.S.A. (Hallberg 1987) and Poland (Kowalik 1987). Inmany countries. it is obse rved that the nitrogen content of groundwate r is increasing withtime. The rate of increase has been determined in Belgium (de Smedt & Loy 1983), Denmark (Overcaard 1985) and Germany (Such1985). It is noted that unconf ined gro undwater , having a direct connection with the atmosphere. is typically being contaminated by nitrates (Krainov et al. 1989). Reduced nitrogenspecies (ammonium and nitrite) are only foundin unconfined groundw ater at the centre of intensively contam inated areas (Klimas & Kadunas1983. Zabulis 1988). The reduced spec iesmay. however. accumulate in deeper aquifersas a result of the reduct ion of nitrates (Botcher& Strebel 1985. Klimas 1990a. Klimas 1991).
The aim of this paper is to demonstrate the
exte nt of nitrogen contaminat ion of groundwater in Lithuania. its lateral and vertical dist ribution. and the distribution of ox idised and reduced nitrogen species in the gro undwater.
Nitrogen contamination common featuresGroundwater contam ination by nitrogen maybe local (point- source ) and regional (diffusesource). Sources of local contamination maybe associated with:
(a) towns and industry: sewerage systems,domestic and industrial waste disposa l. storesof industrial and raw mater ials. anthropogenicdepos its and others.(b) agriculture: stores of fert ilizers and chemicals. silos . manure storag e. large farms . settlement s.
As regards regional contamination there aretwo poss ible sources: polluted atmospheric
NGU · BULL. 424. 1993
deposi tion and agr icultural activity. Burningof foss il fuels and some ferti lizer factoriescontam inate the atmosphere with nitrogencompounds. In agriculture, organ ic and mineral fert ilizers are the main source of nitrogencontam ination (Gustafson 1983, Such 1985,Gerhart 1986, Scheffer & Walther 1988, Zabulis 1988).
Nitrogen is a chemical element of variableoxidation state . In groundwater it may be foundin the form of dissolved gases (NH" N" N,O,NO, NO" N,O,) or ions der ived therefrom (nitrates (NO,'), nitr ites (NO,"). and ammonium(NH,+)). Many of the gaseous nitrogen compounds are relatively soluble in water withoutbeing particularly react ive (N" N,O, NO), although on oxidation, they may react readilywith water, e.g.:2NO + 0 , - 2NO,2NO, + H,O - 2W(aq) + NO,' + NO,'.Ammonia reacts with water to form a basicsolution, i.e.:NH, + H,O - NH/ + OH',but the greater part often remains in the solution in the form of dissolved ammonia (Krainovet al. 1989). Two main factors , oxygen andorgan ic mater ial, control the state of nitrogenin groundwater. The most stable form of nitrogen in oxidised environments is nitrate . In aclosed system , dissolved oxygen is rapidlyused up in the oxidation of organic mater ial,whereafter oxygen from other dissolved spec ies (e.g. SO,= or NO,') is consumed. The reduction of nitrates and nitrites to ammonium occurs after (Le. at a lower Eh) reduction of ironand manganese oxides , but before (Le. at ahigher Eh) the reduct ion of sulphate to sulphide (Krainov et al. 1982). Bacter ial activity isintimately involved in all the trans itions between the various nitrogen species, Le.NO,' ... NO,' ... NH/ .
During the course of such transformations,a certa in port ion of nitrogen is liberated asnitrogen gas (N,), Le., the tota l amount of nitrogen in the system decreases due to the proces ses of biodegradation and biodestruction (Bottcher & Strebel 1985, Wolff et al. 1985, Trudelet al. 1986, Ronen et al. 1987, Zabulis 1988).The geochemical environment, as defined bythe redox potential (Eh) and acidity (pH), determines the distr ibution of the various nitrogenspecies in groundwater (Krainov & Schwetz1987). As the tranformation react ions are equilibrium reactions, all three species (NO,' , NO,',NH,+) are usually found , to a greate r or lesser
Nitrate contamination of groundwater 77
degree , in groundwater at different pH andEh values (Krainov et al. 1989, Klimas 1991).
The mechanism of the transport path ofnitrogen compounds down to groundwater israther compl icated (Gustafson 1983, Gerhart1986, Thiery & Seguin 1986, Scheffer & Waiter 1988b). The main biochemical transformations take place in the soil. The amount ofnitrogen leached out of the soil depends onmany factors : climate , soil-type , quantity offert ilizers , their type and time of application,agricultural pract ice, etc. Biotransformationprocesses cont inue in the unsaturated zone,and some denitr ificat ion may occur , return ingpart of the nitrogen to the atmosphere. Thus ,the concentration of nitrogen compounds inthe unsaturated zone decreases with depth.Also, infiltration of sewage into the groundby means of septic tanks, infiltration plantsand liquid manure spread ing fields is commonly pract ised as a means of treat ing sewageeffluent , and it has been shown that the majority of pollutants, including nitrogen, can reachthe water table (Klimas 1988b). The infiltratedwater initially contam inates the surface layerof the unconfined groundwater. The groundwater velocity, hor izonta l & vert ical dispers ioncoefficients and hydraulic conduct ivity of underlying strata determine the further lateraland vert ical spread ing of the contam ination(Klimas 1990c).
A phenomenon commonly observed in connection with local and regional groundwatercontam ination by nitrogen is that of vert icaland lateral geochem ical zonation (Zabulis1988, Krainov et al. 1989). Typical of vert icalzonation is a decrease in nitrates with depthand a correspond ing increase in ammonium.In instances of regional contamination of deeper conf ined aquifers , the offend ing speciesis typically ammonium, derived from reduct ionof nitrate. In the case of local contaminationa contrary picture has been observed; in thecentre of intensive contamination, ammoniumis usually dominant in near-surface groundwater , with nitrates becoming more common further from the centre . All these cases can bedocumented by concrete examples from lithuania.
MethodsIn all of the following hydrochemical investigations. standard analytical methods have .been applied; pH and Ehhave been measured in the field. and other parameters inthe laboratory following preservation and storage of sarnples. Pilot studies of local groundwater contamination were
78 Algirdas Klimas & Bernardas Paukstys NGU · BULL 424. 1993
Table 1. Some indices of the unconfined groundw ater quality in the region of the Jonava nitric fert ilizer factor y. otethat conc entrations of nitrate and ammonium are referred to in mg NO,' or NH.+/I throughout the paper. rather than mgNl1.
Unconf ined groundwater Number of Numbe r of Water quality indicators (arithmetic mean)sampling point obse rvat ion samples pH Eh NO,- 0 ,- NH.+
(samplingdepth.m) wells (mY) mgn mg/l mg1
Background groundwater qual ity 3 30 7.2 130 0 0 0.2(6 - 12 m)
9.3 170 475 60 3000Below the factor y's 14 25ammon iac water reservoirs(6 - 8 m)
400 19 0.15 2.1Below the factor y's 5 15 7.5emerge ncy storage ponds(8 - 10 m)
46 0.03 1.2Region of polluted prec ipitat ion 7 40 7.4 400(10 - 12 m)
carried out at specially equ ipped observation areas (Jonavanitr ic fert ilizer factory . three pig-b reeding farms. the karstreg ion of North Lithuan ia, etc.)
For the studies of regional pollution of unconfined groundwater . some hund red dr illed wells . and approx imately onethousand dug wells were sampled. Intermediate conf inedand deep conf ined groundwater chemistry studies are based on the sampling resul ts from approx imately 3000 dr illed wells .
Nitroge n compounds were analysed in the laboratoryusing standard methods such as Nesslerization and co lorimetry .
Local contaminationThe Jonava factory for nitric fert ilizers is anexample of especially intensive local industr ialcont amination of gro undw ater by nitrogencompounds (Klimas & Kadunas 1983, Klimaset al. 1988). The factory is built at the intersection of the valleys of two large rivers: theNeris and Sventoji (Fig. 1). Here, in the upperpart of the geological section , alluvial sandand grave l depos its dom inate. The tota l thickness of these sediments is typ ically 15-20 m.The deposit s contain a saturated zone whichis typ ically 5-12 m thick . Among the sou rcesof groundwater con tamination one can name(Table 1):(a) emergency flows from ammoniac waterrese rvoirs and infiltration of contam inatedammoni ac-rich water from emergency ponds.(b) infiltration of contaminated precipitation .
In the region of the factory 's storage reservoirs and ponds , contam inated infiltration waters
mix with confined grou ndwater which discharges in the locality. The latter natura lly has asmall cont ent of dissolved solids, but the cont aminated mixture discharging into the valleysof the above- mentioned rivers is best descr ibed as a high ly minera lized water, containingespec ially high levels of ammonium and sodium (cations) and nitrate, chlor ide and bicar bonate (anions). In the vicin ity of the factory .precipitation is contaminated by ammonia, leading to a nitrate concentrat ion in unconfinedgrou ndwater some tens times higher than thebackground level. The process of nitrif icationof ammonium begins in the atmosphere, continues in soil, and is completed in the aerationzone (Klimas & Zabu lis 1984).
Large catt le-breed ing and pig-bre edingfarms are the legacy of collective agriculturein Lithuania. During the past 15 years . morethan 40 such farm-complexe s have been built. The capacity of the pig-breeding complexesis around 12,000 - 54,000 pigs per year. Themanure accumulated here is remov ed usingwater, and the resultant liquid manure is spread on fields. Due to poor technology, greatquantities of liquid manure accumul ate on thefields. In winter and spring, fields of a limitedarea are intensively manured (up to 700-1100kgN/ha) when soils are still saturated. In thisway , unconfined groundwater can be severelyconta minated (Zabulis 1988).
Table 2. Chemical composition of unconfined groundwater below the manured fields of some piq-breeding farms. TDS =total disso lved solids . Corg = organic carbon .
Location Number of Samp ling Chemical composition of groundwater. mg/l(Aquifer) observat ion depth Arithme tic mean [range of var iatio n)
well s (m) TDS Corg NO,' NO,- NH.+dissolved
Valkin inkai 21 10-13m 400 10 15 0.2 1(sand. thick unsa tura ted zone) [300 -1200) [9-26) [7-710) [0.1-0.3) [0.3-7)Rokai 14 1-3m 700 39 450 1 3(sand, thin unsaturated zone) [400-2200] [17-61] [ 10-900) [0.1-2J [0.4-12)Sirvin ta (sandy loam) 9 5-7m 1300 45 30 2 30
[200-2000) [11-64) [5-300) [0-3) [2-35)
NGU - BULL. 424.1993 Nitrate contam ination of groun dwater 79
N
f
Fig. 2. Trends in pollution of karst groundwater in Lithuania. 1-areas in which karst water was already polluted bynitrogen compounds in 1978-1979; 2-areas in which indices of nitrogen pollution increased by more than a factorof two during a 10 year period.
excess ive nitrate concentrat ions . Even furtherdown-gradient , denitrif ication and dilution leadto an eventual attenuation of nitrate concentrations (Zabulis 1988).
The territory of North Lithuania possessesan outcrop area in excess of 1000 km' ofgypsiferous Upper Devonian depos its (Paukstys 1991). The upper part of these strata iskarstified. Recharge of groundwate r typicallyoccurs via the direct infiltration of precipitationon the outcrop area, and karst wate r discharges into small local rivers. In these gyps iferous rocks, a calcium sulphate groundwater,with a moderate disso lved solids content (2000- 2500 mg/l) is typically found. Upper Devoniansands and sandstones underlying these gyps iferous strata typ ically conta in fresh groundwa ter. Groundwater with in a large area (about400 km') of the gyps iferous depos its is, however, who lly or almost wholly unprotected fromsurface contam ination, and is therefore beingintensively polluted by organic materials or
Table 3. The chemical composi tion of polluted groundwater in the karst region of North Lithuania.
Aquifer Some indices of chemical composit ion, mgll (except Eh, pH)
(Sampling depth, m)TDS Ca++ Mg++ SO,= Cl- Eh(mV) pH NH,+ NO; NO;
Phreatic, sandy loam (boreho le) (10-15 m) 352 61 27 32 12 < 100 6.8 120 < 0.01 2
Phreatic, dolomite (dug well)(10-15 m) 1063 154 64 101 135 330 6.9 < 0.1 < 0.01 180
Phreatic, dolomite {borehole) (20 m) 392 30 31 8 5 150 7.6 30 < 0.01 < 0.5
Deep confined, dolomite (borehole) (40-60 m) 365 22 31 4 5 120 7.8 45 < 0.01 < 0.5
The nitrogen in liquid manure is largely inthe form of ammonium and organ ic nitrogen .If (a) the subso il beneath the manured fieldsis sandy, (b) the unsaturated zone is thick and(c) the manure application is not very intens ive(i.e. less than 300 kgN/ha in tota l), then theunconfined groundwater may escape excessive contamination. Such contam ination as exists is typically in the form of nitrates (Table 2- Valkininkai). Down-grad ient from the manuredfield, denitr ification and dilution by clean infiltration water result in a rapid attenuationof the contamination plume. If, however, themanured fields are underla in by more clayey ,fine grained subso il, with a relatively shallowwater-table, and if manuring is intensive, heavy contamination by ammonium and organ icmaterial is most typical. Down-gradient , activeoxidation of ammonium and organ ic nitrogentakes place in the groundwater, leading to
nitrogen compounds (Fig. 2). This is due toagricultural activity, particu larly the applicationof mineral and organic fert ilizers . Especiallyhighly contam inated groundwater is found inthe vicinity of catt le-breed ing farms with storesof manure, silos , sewage and manure accumulators and fert ilizer storage areas (Klimas &Paukstys 1990) - e.g. the first two rows ofTable 3. The areal distr ibution of contaminatedkarst water areas shows a regular pattern(Fig. 2), reflecting very well the hydrogeological structu re of the kars t. The water is mostconta minated in local areas of recharge (ininterfluves and the upper reaches of small rivers) and least in the zones of discharge ofkarst water (in river valleys). This simplisticpicture is, however, disto rted by the abstraction of groundwater (Paukstys 1991).
The karstic groundwater is typically contam inated by ammonium, and the thermodynamic
80 Algirdas Klimas & Bernardas Pauk~tys
Fig . 3. Unconfined groundw ater pollution and soil bonitetin Lithuania. 1-highly polluted unco nf ined groundwater;2- soil bonitet in the range 50· 100 (of 1st-5th class).
and biochemical stabilty of that species isconsistent with a low redox potential (below200 mV) and a neutral pH, around 7 (Krainovet al. 1989). In the water from wells in areaswhere the water has good access to the atmosphere, Eh values are much larger and nitratesprevail.
Regional pollutionUnconfined groundwaterIn Lithuania, shallow unconf ined groundwate rtypica lly exists within Holocene (alluvial, aeoli-
NGU - BULL 424. 1993
an, marine sand) and Pleistocene (glacial andfluviolacial sand, loam, and sandy loam) deposits. The chemical composition of such watersis very variable. It is, however, possible toshow that the level of contamination is twoto three times greater below more clayey,poorly-drained areas than below sandier, welldrained plains (Kondratas & Mikalauskas 1973,Klimas 1991). This difference is both directlyand indirectly connected with the geology, asit is typically the more clayey areas which aremost fert ile (soil bonitet of 1st-5th class: note- in Lithuania, 10 classes of soil bonitet arein use) and thus the locations of most intensive agriculture (Fig.3).
In Lithuania, the nitrate concentration inshallow groundwate r varies widely, fromaround zero to several hundred mg/l, but onecan state that beneath about one third of thecountry the nitrate in unconfined groundwaterexceeds the permissible drinking water standard (45 mg/l). Only in one eighth of the territory is the concentration less than 10 mgll(Fig. 4a). Low nitrate concentrations are foundonly in the Coasta l lowland and South-EasternLithuanian plains, where the agricultural activity is not intense, and the grou ndwater resources are large (Juodkazis & Klimas 1991). Theorganic material conten t of groundwate r issimilarly distributed: permanganate oxidationin the regions contaminated by nitrates gener-
Fig. 4 . Nitrate (a, b. c) and ammonium (d. e. f) concentrations in unconfined (a. d), intermediate confined (b. el . and deepcon fined groundwater (c, f) in Lithu ania.
NGU • BULL. 424. 1993
ally exceeds 5 mg/I and in some places itreaches 10 mg/1.
The amount of ammonium in unconfinedgroundwater is comparatively small ; it exceeds0.2 mg/l over only 10-15% of the terr itory (Fig.4d).
Intermediate confined groundwaterThis is the transitional type of groundwaterbetween unconfined and deep confinedgroundwater. It is typ ically found in intermorainic deposits (Klimas 1991). In Lithuania, oneor two such aquifers can typically be found ina vertical section through the Quaternary deposits , but in some places up to five or six canoccur . They are usually hydraulically interconnected and may have good hydraulic contactwith both underlying artes ian water and overly ing unconf ined groundwater.
Intermediate confined water is commonlyonly minimally protected against anthropogenic pollution (Klimas 1990a). Therefore, whereunconfined groundwater is contaminated, intermediate confined groundwater is generally alsocontaminated (Fig. 4a and b). It is clear thatthis occurs where contaminated unconfinedgroundwater recharges intermed iate confinedaquifers (Le. a downward hydraulic gradientfrom unconfined to intermediate confined aquifers), most frequently in highlands. On thecontrary, in plains and river valleys, whereunconfined groundwater is sometimes highlycontaminated , intermediate confined groundwater usually remains clean because the latteris protected by conf ining strata and generallyby an upward hydraulic gradient.
The contamination pattern for intermediateconf ined aquifers is shown in Figs. 4b ande. Comparison of the diagrams shows thatincreased nitrate contents in intermed iate confined water are found , not in Middle Lithuaniawhere unconfined groundwater contaminationis greatest, but in the marginal parts of therepub lic, especially in regions of high topog raphy (Le., in the recharge areas of intermediateconfined aquifers) . It is clear that the areasof intermediate confined groun dwater contaminated by nitrates are much less extensive thanthose of unconfined groundwater. Nitrate concentrations in intermediate conf ined grou ndwater rarely exceed 10 mg/I wherea s in unconfined groundwater the value is usually 3-4times greater.
Compar ison of Figs. 4d and 4e indicatesthat intermediate conf ined groundwater is
Nitrate contamination of groundwater 81
more areally extens ively contam inated byammonium than unconfined groundwater. These areas of ammonium contam ination in unconfined and intermediate confined groundwaterdo not coincide. In intermediate conf ined aquifers the high ammonium values are found inareas where groundwater is better isolatedfrom unconfined groundwater (Iimnoglacial plains, moraine dominated areas and the Samogitian highlands - see Fig. 1).
Deep confined (artesian)groundwaterIn Lithuania, deep, confined water can be foundin deposits of all geological ages, from Cambrian sandsto nes to Paleogene and Neogenesands (Juodkazis 1989). Such deep confinedgroundwater is one of the main sources forlarge, centralised water supplies in Lithuania.Only a small proportion of deep conf ined aquifers are, however, reliably isolated and protected from surface pollution. In recharge areas(topographical highs) deep confined groundwater is recharged from intermediate conf inedand unconfined groundwater. Due to intensiveexploitation in West and Middle Lithuan ia, large areas of depressed groundwater headhave been formed . Thus , some areas of natural dischar ge of artesian water have becomeareas of recharge, creating conditions suitablefor the downward migration of polluted waterto deeper confined aquifers (Klimas 1979).
Investigations reveal that deep confinedwater is only contaminated by nitrates to alimited extent (Fig. 4). The few areas of deepconfin ed water with elevated nitrate concentrations do not coincide with areas of unconfinedgroundwater and intermediate conf ined waterwhich are highly contam inated by nitrates .Klimas (1 991) has noted generally higher concentrations of ammonium in deep conf inedwaters than in intermediate confined or unconfined groundwater (Fig. 4f). The areas in whichammonium concentrat ion exceeds 1 mg/I account for almost 20% of the territory of Lithuania. Ammonium accumulates comparativelywell in the isolated deep conf ined aquifers ofWest Lithuania but is practica lly absent in themuch less isolated, East Lithuanian , deepconfined aquifers. A similar pattern can alsobe recognised in the distribution of organ icmaterial in deep confined water. It thus appears that the low nitrate and elevated ammonium contents typically found in deep confined
82 Algirdas Klimas & Bernardas Paukstys GU . BULL. 424. 1993
gro undwater are the result of the chemicalreduction of nitrate to ammonium (Klimas etal. 1988, Krainov et al. 1988, Klimas 1991).
DiscussionInvestigations of local and regiona l groundwater po llution by nitrogen compounds in lithuania revea l regularities in the patt ern of contamination and allow one to predict its future evolution.
Redox potent ial (Eh) and acidity (pH) valuesreflect the processes of migrat ion and transform ation of nitrogen compou nds in groundwater. Unconf ined groundwater aquifers usuallyenjoy a good connection with the atmosp hereand therefo re exh ibit high dissolved oxygenlevels, commonly up to 7-10 mg/l, Eh typicallyexceeds +200 mV and pH is around 7. Insuch water one typically finds a limited rangeof nitrate conce ntrat ion (2-10 mg/l). In centresof intensive contamination, prac tically all theoxygen is con sumed by the oxidat ion of orga nic contaminants. The amou nts of unox idisedorg anic material and ammo nium show elevatedvalues in such situations (see Table 2), and acorrespond ing reduction in Eh and nitrates(see Table 3) due to biochemical reductionby ammonification bacteria. The values of pHfound at such contaminated localities varywidely (Fig. 5). These chemica l cond itions areespec ially not iceab le in contaminated, uncon fined groundwater aquifers occurring in clayey, poorly-drained areas .
Fig. 5 is comp iled from stud ies carried outin fields spr ayed with liquid pig-manu re(300-600 kgN/ha) covering an area of 150hectares. Unconfined groundwater is found ata depth of 0-5 m in sand, morainic sandy loamand loam deposits . It can be seen that thelevel of contam inat ion of unconfined groundwater , composit ion of the contamination components and the values of Eh-pH of unconfinedgroundwater found within the comparativelysmall area vary greatly. A patte rn can, however, be identi fied. First ly, the nitrate concentra tion in sandy deposits is dist inctly lower thanin clayey one s (Fig. 5c). Furthermore, increases in NO,'concentrations correspond to increases in Eh and pH. In addition. the concentrations of ammon ium and iron show a correspond ence, and are related to depressed Ehand pH values. The depe ndence of ammoniumand iron on lithology is not so dist inct as isthe case for nitrates.
A similar pattern can also be observed in
pH8
~Ti ll
,
, ,I: "11 1:1 : ' I
I ,
7
EJ, I SandI I
I
20
30
10
40
Fig. 5. Eh,pH diagrams for a) ammonium b) iron and c)nitrate in polluted , unconf ined Lithuanian groundwater .
NH~ .
mg/ I
NGU - BULL. 424. 1993 Nitrate contamination of groundwater 83
Fig. 6. Ammonium concentrations plotted against depth forthe gro undw ater of the Lithuan ian karst reg ion.
the case of regional unconfined groundwatercontamination. It has already been demonstrated that nitrate tends to be the dominant nitrogen spec ies in unconf ined groundwater in Lithuania. Only in limnoglacial clayey formationscan elevated concentrations of ammonium befound (Fig. 4d). One exception, however, isthe karst region of North Lithuania where fissured dolomites with interbeds and lenses ofgypsum outcrop (Klimas & Paukstys 1990,Paukstys 1991). The groundwater within theseis stro ngly polluted with organic material andcontains pract ically no dissolved oxygen. Redox potentials are typically lowered to 60-180mV, and iron concentrations can reach 8mgll (Paukstys 1991). Generation of methaneand hydrog en sulphide can also be observed.Ammonium dominates among nitrogen compounds. The variation of its concentration withdepth is presented in Fig. 6.
Fig. 6 demons trates that in cases of intensive contam ination, an inversion of oxidat ionreduction zonation can take place: a zone lacking oxygen, with low Eh values, and enrichedin ammonium is formed above an oxidisedzone (areas 2 on Fig. 2).
On a regional scale, however, a norma lzonat ion (Fig. 4) is typically observed, i.e. anupper, oxidised, nitrate zone over a deeperreduced ammonium-dominated zone. The factthat the amounts of ammonium and organicmaterial in intermediate conf ined and deepconf ined aquifers are increasing with time indicates that the phenomenon is really connectedwith anthropogenic pollution. This increase isdescr ibed by the following relations (Klimas1991):
in intermediate conf ined waterNH: = 0.012 t + 0.411 (r = 0.39)
P = 0.131 t + 1.61 (r = 0.82)
in deep confined waterNH: = 0.0405 t - 0.02 (r = 0.46)
P = 0.142 t + 0.32 (r = 0.75)where P = permanganate oxidation mg 0 ,/1,character ising the amount of readily ox idisable organic material in watert = time from the beginning of the analysis(1958) period, in years .r = correlation coeff icient, significance level0.5 % .
From these equations it follows that in deepconfined water organic material has been present since before 1958 (P "* 0, when t = 0),while the process of the accumulat ion of ammonium has begun later (NH. ~ 0, when t ~0). Furthermore, the corre lation coeffic ient forammonium is half that for organic material.This is presumably due to the instability ofammonium; with access to oxygen it readilyoxidises to nitr ite and eventually to nitrate.
The exp loitation of conf ined groundwatercan great ly alter the geochemical environmentwithin aquifers. It can induce leakage ofgrou ndwater of a different chemical composition from strata above and below the exploitedaquifer (Klimas 1979). For example:
(1) water leaking to the aquifer from aboveis commonly enriched in oxygen and may thuslead to a progress ive increase in the nitrateconcentration in the exploited aquifer.
(2) water leaking to the aquifer from abovemay, however, be strongly polluted with organic material and nitrogen compounds, leadingto consumption of oxyge n in the exploitedaquifer and increasing concentration of ammonium.
(3) water leaking to the aquifer from below(from deeper hor izons) is usually oxygen poor, leading to decreasing values of Eh andaccumulation of ammonium in the exploitedaquifer. All these cases can be observed atgroundwater works in Lithuania (Klimas 1973,1991).
Biotransformation of nitrogen compounds ,accumulation of unoxidised organic material,and a decrease in Eh can greatly alter thegeochemical environment in an aquifer, suchthat favourable conditions for the mobilisationof tox ic microelements (including heavy metals) may be formed in these aquifers (Krainov& Schwetz 1987, Klimas 1988a).
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60
80
84 Algirdas Klimas & Bernardas Paukstys
ConclusionsStudies of groundwater pollution by nitrogencompounds have a long history. The information presented in this paper has been collected from groundwater monitor ing data andfrom special hydrochemical maps compiled forindividual aquifers . The analysis 0 1 this material indicates a complicated and rather ominousview of the pollut ion of the Lithuanian groundwate r environment by nitrogen compounds .On the whole , it coincides rather well with theobservat ions of such pollution in many othercountries. Despite the complexity of the processes occurring in the subsurface, certainpatte rns can be identified in the data:1) Groundwater is contaminated by nitrogen
compounds locally and on a regional scale.There are many sources of local pollution,but only two sources of regional pollution- atmosp heric pollution and agriculturalactivity.
2) Nitrogen compounds take an active part inbiochemical react ions, and their spsc iationand concentrations in grou ndwater canvary. Eh and pH conditions are decisive indetermining whether nitrate or ammon iumis the dominant species.
3) Patterns in nitrate and ammonium distr ibution can be detected. These are expressedas vert ical and horizontal zonation of redoxpotential and nitrogen speciation. In upperaquifer hor izons , and in recharge areas ofdeeper aquifers , nitrates dominate and Ehis typ ically greater than +200 mY. In deeper aquifers, and espec ially in their trans itand discharge areas, ammonium is dom inant in gro undwater, with Eh typically lessthan +200 mY.
4) In unconf ined groundwater, with a comparatively good connection to the atmosphereand a suff icient amount of disso lved oxy gen, nitrate is usually dominant. Only in the
GU - BULL. 424. 1993
centr es of intensive pollution (e.g. manurespreading fields) where microorganisms arenot able to oxidise organic material andnitrogen compounds, does ammonium dominate in unconfined groun dwater.
5) The amount of nitrogen compounds in unconfi ned groundwater may decrease comparatively quickly due to denitrification, dilution by 'clean' precipitat ion (infiltration recharg e). Thes e processes proceed quickerin sandy deposits and more slowly in clayey deposits. Unconfined groundwater istherefore most strongly polluted by nitratein the clayey plains region of Middle lithuania.
6) In deeper aquifers wher e there is an increase in concentrat ions of unoxidised organicmaterial due to progressive pollution, thegroundwater environment becomes steadilymore reduc ing, Eh values fall and nitrateis transformed to nitr ite and eventuallyammon ium. The concentration of ammonium increases with time.
7) The increasingly reducing environment indeeper aquifers is one of the main reasonsfor the accumu lation of some metals ingroundwater. Major changes in geochemical condit ions can be caused by groundwater exploitation. During such exploitat ion,not only regional groundwater flow patterns , but also hydroch.emical zonation aredisturbed. Exploitat ion can thus seriouslyinfluence the distr ibut ion, concentrationsand speciation of nitrogen com pounds ingroun dwater.
AcknowledgementsDavid Banks of NGU. Trondnerrn, encouraged us to writetrus paper and kind ly helped with Eng lish language corr ecnon s for which we are mo st grat eful. We are also grate fulto Pro!. Dr. V. Juodka zis (Vilnius) for read ing the Lithuanianversion of the manusc ript. and to Dr. V. Zakutin (Moscow)for giving permission to use some of the results from hisstudies of gro undwater qua lity In Lithuania.
NGU - BULL. 424.1 993
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Manuscript received August 1992; final revised typescript accep ted February 1993.