, Volume 646, Issue 1, pp 61–72 | Cite as

Drought-induced changes in nutrient concentrations and retention in two shallow Mediterranean lakes subjected to different degrees of management



While extensive knowledge exists on the relationship between nutrient loading and nutrient concentrations in lakes in the cold temperate region, few studies have been conducted in warm lakes, not least in warm arid lakes. This is unfortunate as a larger proportion of the world’s lakes will be situated in arid climates in the future due to climate change and a larger proportion will suffer from a higher frequency of intensive drought. We conducted a comprehensive 11–13 year mass balance study in two interconnected shallow Mediterranean lakes in Turkey, covering a period with substantial changes in climate conditions. The upstream lake was only affected by natural changes in nutrient loading, while the downstream lake was additionally influenced by sewage diversion and restoration by fish removal. Contrasting to experience from north temperate lakes we found an increase in in-lake concentrations of total phosphorus and inorganic nitrogen (ammonia as well as nitrate) in dry years despite lower external nutrient loading, and submerged macrophytes did not increase the nitrogen retention capacity of the lakes. In contrast, fish removal modulated the nitrogen concentration as in north temperate lakes, but the effect was not long-lasting. Our results suggest that climate warming reduces the nutrient retention capacity of shallow lakes in the Mediterranean and exacerbates eutrophication. Lower thresholds of nutrient loading for shifting turbid shallow lakes to a clear water state are therefore to be expected in arid zones in a future warmer climate, with important management implications.


Arid regions Nitrogen dynamics Biomanipulation Climate change Eutrophication Water level fluctuation 


Riverine phosphorus and nitrogen are retained and nitrate is denitrified during the passage of lakes, the retention and loss percentage being particularly affected by hydraulic retention time (e.g. OECD, 1982; Bachmann, 1984; Lijklema et al., 1989), lake depth (Windolf et al., 1996) and trophic structure (Jeppesen et al., 1998). Several simple empirical mass balance models relating lake concentrations to external loading on an annual (e.g. OECD, 1982; Bachmann, 1984; Saunders & Kalff, 2001) or seasonal (Windolf et al., 1996) scale have been developed and extensively used for lake management purposes. However, these models were constructed mainly for north temperate lakes.

Hydrology is an important element in nutrient mass balances, not least for shallow lakes located in Mediterranean climatic regions. Such lakes are subjected to large variations in water level determined by naturally intra- and interannual variations in rainfall and groundwater discharge or re-charge in alternating drought and wet periods (Coops et al., 2003; Alvarez-Cobelas et al., 2005; Beklioglu et al., 2007). Such changes in hydrology may have major implications for nutrient dynamics and nutrient retention in lakes, not only directly through changes in loading and hydraulic retention time, but also indirectly through alterations in trophic structure, including changes in macrophyte coverage (Beklioglu et al., 2006; Beklioglu & Tan, 2008). Variations in temperature may also affect trophic structure and oxygen concentrations, the latter being a sensitive variable (in addition to temperature) for the phosphate release from the sediment (Jensen & Andersen, 1992; Søndergaard et al., 2003) and for nitrification/denitrification (Windolf et al., 1996; Eriksson & Weisner, 1997). However, only few mass balances exist for arid and semi-arid lakes (e.g. Gophen et al., 1990; Jossette et al., 1999; Romero et al., 2002; Romo et al., 2005) and studies considering the impact of varying hydrological conditions (e.g. drought and wet periods) from dry regions are particularly rare. This is unfortunate as a larger proportion of the world’s lakes are predicted to be subjected to major inter-annual and seasonal variations in hydrology in the future due to global warming. Moreover, lack of data from such regions makes global balances uncertain.

We conducted a comprehensive 11–13 year mass balance study on total phosphorus and inorganic nitrogen and phosphate in two interconnected shallow Mediterranean lakes in Turkey during wet and dry periods entailing substantial changes in climate conditions. Upstream Lake Mogan was only affected by natural changes in nutrient loading determined by variations in hydrology, while downstream Lake Eymir was additionally influenced by sewage effluent diversion conducted in 1995 and restoration by fish removal, which was undertaken twice during the study period (1998–1999 and 2006–2007).

Materials and methods

Study sites

Lake Mogan and Lake Eymir are two interconnected shallow lakes located in the Central Anatolia, 20 km south of Ankara, Turkey (Fig. 1) The region has the Central Anatolian semi-arid climatic conditions, with most of the rain falling during late winter and spring and with hot summers. Thirty years (1975–2006) of average air temperatures and precipitation are 21.5 ± 0.8°C and 384 ± 104 mm, respectively (Turkish State Meteorological Service).
Fig. 1

Map of Turkey showing the location of Lakes Mogan and Eymir with the sampling sites given in filled circular

Lake Mogan

Lake Mogan is large and shallow (drainage area: 925 km2, surface area: 5.4–6 km2, Zmax: 3.5 m, Zmean: 2.1 m, 39°47′N 32°47′E). The lake is mainly fed by four main inflows, the Sukesen brook in the north, the Gölcük and Yavrucak brooks in the west and the Çölovasi brook in the east. The outflow runs into Lake Eymir through a canal and a wetland in the north.

Although we did not have quantitative data on macrophytes for the period 1997–2000, the lake had extensive macrophyte beds exhibiting pondweed, Potamogeton pectinatus (Linnaeus 1753) and Chara sp. (Beklioglu personal observation). From 2001 to 2003, the seasonal maximum coverage of submerged plants ranged from 20 to 90% among years, being particularly influenced by variations in water level, especially in spring (Tan & Beklioglu, 2005, 2006; Beklioglu et al., 2006; Fig. 2). In 2004, a coverage decline occurred, coinciding with higher levels of chlorophyll a and suspended solids and lower Secchi depths (Fig. 2). Phytoplankton was dominated by cyanobacteria (dominated by Merismopedia tenuissima, Lemmermann 1898) throughout the study period and zooplankton mainly consisted of Arctodiaptomus bacillifer (Koelbel 1885) from 1997 to 2003, after which rotifers became dominant (Özen & Beklioglu, unpublished data). Fish data are sparse, but pike (Esox lucius Linnaeus, 1758) used to dominate until mid-2000 (DSI, 1993; ÖÇKK, 2002; Manav & Yerli, 2008). Catfish (Siluris glanis, Linnaeus 1758) was also caught during this period. Investigations undertaken in 2006 and 2007 showed that common carp (Cyprinus carpio, Linnaeus 1758) and tench (Tinca tinca, Linnaeus 1758) were now the most abundant species. In addition, bleak (Alburnus escherichii, Steindachner 1897) appeared in the catches.
Fig. 2

Water level and Hydraulic Residence Time (HRT) (a, b), annual mean chlorophyll a (c, d), annual mean Secchi depth (e, f) and percentage Plant Volume Infested (PVI) (late summer) (g, h) in Lake Mogan and Lake Eymir during the study period. For Lake Eymir 1 = period of external loading reduction, 2 = period of biomanipulation, 3 = post manipulation period and 4 = period with repeated biomanipulation

Lake Eymir

Lake Eymir is a smaller downstream situated lake (drainage area: 971 km2, surface area: 1.20–1.25 km2, Zmax: 4.3–6 m, Zmean: 2.6–3.2 m; 39°57′N, 32°53′E). The lake receives most of its water from Lake Mogan (Eymir Inflow 1). The other inflow is Kışlakçı brook and the outflow is Eymir Out. The lake received raw sewage effluents for more than 25 years (Altınbilek et al., 1995) until diversion in 1995. Before diversion, Inflow 1 constituted 89% of the total external loading of TP. The fish stock was dominated by tench and common carp in 1997–1998. To reinforce recovery after nutrient loading reduction fish biomanipulation was undertaken during 1998–1999. Fifty percent of the stock of common carp and tench was removed and a ban on pike angling (Esox lucius) was introduced and had a major effect on the lake water quality: a 2-fold and 4-fold decrease in chlorophyll a and suspended solids, respectively, and a 2.5-fold increase in annual Secchi depth occurred (Beklioglu et al., 2003). Seasonal maximum coverage of submerged macrophytes was low (2.5%) before biomanipulation, but expanded after (40–90% coverage) (Fig. 2), being particularly high in the dry year 2001. However, 5 years after the biomanipulation, the fish biomass increased again to the pre-manipulation level, and in 2004 the lake shifted back to a turbid state with scarce submerged vegetation cover (Fig. 2) and higher biomass of both tench and carp, and lower biomass of pike (Özen, 2006). Following a new biomanipulation in 2006–2007 (removing tench and carp) the lake water quality improved (a 2-fold and 1.5-fold decrease in chlorophyll a and suspended solids, respectively, and a 50% increase in annual Secchi depth), though no major change was observed in macrophyte coverage. The phytoplankton community was dominated by chlorophytes during the clearwater period and by cyanobacteria (dominated by Anabaena circinalis, Rabenhorst 1863) during the turbid period. The zooplankton community was largely dominated by A. bacillifer and Daphnia pulex (de Geer 1778) from 1997 until 2003 and by rotifers from 2004 to 2006. In 2007 the zooplankton community was characterised by dominance of D. pulex and D. magna (Strauss 1820).


Water samples were collected from March 1997 to September 2007 in both lakes. Sampling was conducted fortnightly in spring, summer and autumn and monthly in winter. For further details about sampling and the methodology used for analyses of TP, NH4–N, NO2– and NO3–N (see Beklioglu et al. 1999, 2003).

We calculated monthly water and nutrient budgets. For each components of a water budget (inflows (I), precipitation (P), outflows (O) and evaporation (E)) we first calculated:
$$ B = {\frac{\Updelta V}{\Updelta t}} = I + P - O - E $$
where V is the lake volume, and ΔVt is the change in lake volume per unit of time (t).
We then estimated groundwater input or output as:
$$ G = \delta V - B $$

δ V is the change observed in lake volume and B is derived from Eq. 1. We then summed I, P, O, E and G up to annual values.

The lake level, given in meters above sea level (m. a. s. l.), was recorded daily from a fixed gauge positioned at the southwest corner of Lake Mogan, and at the north-east shore of Lake Eymir. Data on water levels and discharge for the inflows and the outflows of the lakes were obtained from the General Directorate of Electrical Power, Resource Survey and Development Administration (EIE, 2007). The volume of the lakes was calculated using the bathymetric map constructed in 2000. Monthly air temperature, rainfall and evaporation data were recorded at a meteorological station located within the catchments of the lakes. The hydraulic residence time was estimated by dividing the lake volume (Vlake) by the volume of water entering the lake (Vin) per unit of time.

The following equation was used to calculate the nutrient budget:
$$ \partial{\text{Lake}} = {\text{ Inputs }}\left( {I + P} \right) -{\text{Outputs }}\left( O \right) \pm G $$

As for the water budget, the monthly nutrient budget was constructed first and then summed up to annual values. The DIN concentration for precipitation was 80 μg l−1 (Tuncer et al., 2001). The TP concentration of the precipitation was negligible (Altınbilek et al., 1995) and not included. Groundwater concentrations of TP and DIN were 24 and 3,423 μg l−1, respectively (Altınbilek et al., 1995). The in-lake TP and DIN concentrations were used for water entering the groundwater.

Nutrient retention on an annual basis was calculated using the following equation:
$$ {\text{Retention }} = {\text{ Total annual input }} - {\text{ mass change in the water column }} - {\text{ total annual output}} . $$
The predicted annual mean TP concentrations were calculated using the Vollenweider (1976) equation:
$$ {\text{TP}}_{\text{lake}} = {\text{ TP}}_{\text{in }} / ( { 1+ \surd {\text{tw}}} ) $$
where tw is the hydraulic residence time (year), TPin the discharge weighted annual mean TP concentration in inlets, and TPlake the annual mean lake concentration.


Water budget

The two lakes were subjected to major interannual variations in water balance (Fig. 2a, b).

Lake Mogan

The annual mean lake volume was 11.5–15.0 km3 (Fig. 3a) reflecting a variation in water level of 0.73 ± 0.27 m a.s.l. The total inflow varied substantially from 0.5 to 18.5 km3 year−1 (Fig. 2a) and the hydraulic residence time ranged between 0.7 and 6.9 years (Fig. 1a). Precipitation contributed with 1.8–3.4 km3 year−1 (Fig. 3a). The highest outflow was recorded in 2000, while no outflow was recorded from 2004 and onwards (Fig. 3a). Evaporation was a major source of water loss, being 44–65% of the lake volume annually (Fig. 3a).
Fig. 3

Water, total phosphorus and DIN balances in a Lake Mogan and b Lake Eymir showing the annual input and output as well as the annual mean in-lake concentration of the various nutrients. Dry years are 2001 and 2003–2007

Lake Eymir

The annual mean lake volume ranged from 2.7 to 4.1 km3 (Fig. 3b) and the mean amplitude of the water level fluctuation was 0.9 ± 0.3 m a.s.l. from 1993 to 2007. The contribution of inflows varied from 0.2–16.6 km3 year−1(Fig. 3b). The precipitation contribution became critical in the low water level years (0.2–0.6 km3 year−1) (Fig. 3b). The outflow followed the pattern for Lake Mogan and completely dried out from 2004 and onwards (Fig. 3b). Loss by evaporation was 27–42% of the lake volume annually and the hydraulic residence time was 0.2–13.5 year (Fig. 2b).

Phosphorous budget

Lake Mogan

The external TP input varied markedly among years (Fig. 3a). The inflows ranged from 0.89 g m−2 year−1 (2000) to 0.024 g m−2 year−1 (2007). Groundwater inflow contributed to the budget during the dry years 2005–2007. The outflow varied from 0.26 to 0.008 g m−2 year−1 until the outlet dried out in 2004. The low water level recorded in 2001 and the relatively low input from the inlets coincided with the decrease in the observed in-lake TP to 54 μg l−1, the lowest of the study period. The highest in-lake TP concentration was found in the dry years (maximum 120 μg l−1 in 2004) despite that the load via inflows then was at its lowest. The observed and predicted in-lake TP values were relatively similar up to 2003, excluding the high input year 2000. However, from 2003 and onwards the predicted TP was much lower than the value observed, indicating high internal loading (Fig. 3a). Net retention of TP in the lake ranged between −0.04 g m−2 year−1 in 1998 to 0.75 g m−2 year−1 in 2000 (Fig. 4a). Also in-lake SRP was overall highest in dry years (Fig. 5a).
Fig. 4

Annual retention versus external loading of total phosphorus and orthophosphate in a Lake Mogan and b Lake Eymir. The 1:1 line is also shown

Fig. 5

Mass balance of inorganic nitrogen and soluble reactive phosphate from a Lake Mogan and b Lake Eymir showing annual input and output as well as the annual mean in-lake inorganic concentration of various nutrients. Dry years are 2001 and 2003–2007

Lake Eymir

The annual TP budget was calculated for a period of 13 years covering 1993–1995 and 1997–2007 (Fig. 3b). Before sewage effluent diversion in 1995, the loading from Inflow I, the major source of TP, was 5.2 g m−2 year−1 and the observed annual mean in-lake TP concentration was 686 μg l−1. Following effluent diversion, the TP loading decreased 16-fold and the in-lake TP concentration 2-fold, followed by an increase during 1999, coinciding with higher hydraulic loading. After fish removal, undertaken during 1998–1999, in-lake TP decreased to172 μg l−1, followed by a major increase during the low water level years (2001, 2004–2007) despite low external TP loading levels. The in-lake TP almost doubled, from 172 μg l−1 in 2000 to 311 μg l−1 in 2001 when the lake volume and water level were at their lowest. A major peak in in-lake TP of 528 μg l−1 coincided with an almost disappearance of submerged macrophytes (Fig. 2h). Following the second biomanipulation, in 2006, when the lake volume and water level exhibited a slight increase, in-lake TP decreased markedly to 243 μg l−1, but in 2007 when the water level was at its lowest and the residence time was at its highest, TP increased again to 337 μg l−1. The predicted annual mean in-lake TP concentration remained above the observed in-lake TP concentration during years with high loading, but was far lower than the level measured during the dry years (Fig. 3b). Net retention of TP in the lake ranged between −1.67 g m−2 year−1 in 1999 to 0.95 g m−2 year−1 in 2002 (Fig. 4b). Also in-lake SRP showed high among-year variability that largely followed the variation in TP (Fig. 5b).

Dissolved inorganic nitrogen budget

Lake Mogan

Major changes also occurred in dissolved inorganic nitrogen loading among years (Fig. 3a). The highest total DIN input of 2.8 g m−2 year−1 was recorded in 1998 and the lowest was 0.030 g m−2 year−1 in 2007. The contribution from groundwater varied between 0.003 and 1.14 g m−2 year−1 and from precipitation between 0.014 and 0.090 g m−2 year−1. Outflow ranged from 0.29 g m−2 year−1 (2000) to zero from 2004 and onwards. The in-lake DIN concentrations were highest from 2001 and onwards, coinciding with low water level and low DIN loading. In-lake nitrate concentrations were highest in the dry years (2001 and 2003–2007), in-lake ammonia being more variable but overall highest in the dry years (Fig. 5a). A high proportion of the in-lake DIN consisted of ammonium (Fig. 6a), but tended to be lower in 2006–2007 despite lower oxygen concentrations. The DIN loss in the lake was high and almost equal to the input at high loading, while being more variable at lower loading and negative at the lowest input. The variability is mostly attributed to variation in ammonium retention as almost all nitrate entering the lake was lost (Fig. 7).
Fig. 6

Annual mean concentrations of nitrate, ammonium and dissolved oxygen in a Lake Mogan and b Lake Eymir. Dry years are 2001 and 2003–2007

Fig. 7

Annual retention versus external loading of dissolved inorganic N, nitrate and ammonium in a Lake Mogan and b Lake Eymir. The 1:1 line is also shown

Lake Eymir

Mass balances were conducted for dissolved inorganic nitrogen for the periods 1993–1995 and 1997–2007 (Fig. 3b). The DIN load via inflows and the in-lake DIN concentrations were highest before the sewage effluent diversion. Following the effluent diversion, the DIN load via inflow fell to 0.76 g m−2 year−1 and the in-lake DIN concentration decreased 11-fold. Moreover, following fish removal a further 1.5-fold reduction was found. However, it increased again from 2001 and onwards despite low external loading. The highest total input was 22.7 g m−2 year−1, recorded before the sewage effluent diversion, and the lowest was 0.015 g m−2 year−1 recorded in 2007. The groundwater contribution varied between 0.019 and 0.85 g m−2 year−1. The contribution from precipitation became significant during the drought periods. In-lake nitrate and ammonium declined (and thus DIN) substantially following the drastic external loading reduction in the 90’s, but increased again following biomanipulation and recovery of the macrophytes and remained high during the dry years (Fig. 3b) coinciding with low or negative P retention on an annual basis (Fig. 4b). As for Lake Mogan a high proportion of in-lake DIN consisted of ammonium (Fig. 6b). The proportion of ammonium tended to be higher than in Lake Mogan, coinciding with an overall lower oxygen concentration. DIN loss in the lake was high but more variable relative to external loading than in Lake Mogan, and the variability is here also attributed to both variations in ammonium and to nitrate retention in the lake; negative retention occurring in three of the study years (Fig. 7).


The key finding of our study of these two eutrophic warm temperate lakes are: (i) the concentrations of TP and DIN (ammonium as well as nitrate) increased in dry years despite lower external nutrient loading, which contradicts observations from cold temperate lakes; (ii) unlike in cold temperate lakes, extensive growth of submerged macrophytes did not result in lower inorganic N concentrations, and (iii) as in north temperate lakes fish removal enhanced the N retention, but the effect was not long-lasting. These results suggest that climate warming will enhance the risk of eutrophication in shallow lakes in the Mediterranean climatic region in a future warmer and drier climate. This is supported by a comparative study of 10 shallow Turkish lakes showing an average 11-fold increase in chlorophyll a concentrations from the regular year 2004 to the dry year 2007 (Beklioglu & Özen, 2008).

Our study covered a period with substantial changes in precipitation and runoff that markedly affected the water and nutrient balances of the lakes. While inflows were the major nutrient sources in wet years, precipitation and groundwater inputs were most important in dry years. A 20 and 25% decrease in lake volume and a 5- and 10-fold increase in hydraulic residence occurred during the dry periods due to low inflows and high evaporation. These changes had major implications for the nutrient budgets, most dramatically in Lake Eymir due also to a construction of a new higher sluice gate in Lake Mogan in 2003, implying less water overflow to Lake Eymir.

In both lakes, the in-lake TP concentration was, as expected, relatively high in years with high external loading, that is the wet years, and in Lake Eymir also in years with high sewage input (before 1995). However, in-lake TP was also high in dry years with low external input due to high evaporation and higher internal loading per unit of lake volume, likely exacerbated also by a higher temperature-mediated release as seen in other studies (Jensen et al., 2006). The mass balances clearly show that during the dry periods, in-lake TP became more dependent on internal processes (evaporation and internal loading) than on the external loading. Accordingly, we found predicted in-lake TP concentrations using the Vollenweider equation (Eq. 4) to severely underestimate the annual mean TP concentrations in the dry years in both lakes, while it predicted reasonably well the concentrations in the wet year except after sudden changes in loading.

The TP balance and TP concentrations in Lake Eymir were likely also affected by biomanipulation. Thus, a 2.5-fold reduction in in-lake TP occurred following the 50% reduction in carp and tench biomass. Similar high reductions have been seen in other biomanipulated European lakes (Hansson et al., 1998; Søndergaard et al., 2007, 2008), which has been attributed to reduced fish resuspension and decreased internal loading of phosphorus, the latter mediated by reduced sedimentation of algae (less oxygen demand), less P bound in phytoplankton and increased benthic algae production (Hansson, 1990; Søndergaard et al., 2003). Colonization of submerged plants may have contributed as well, since the vegetation coverage increased from 6% in the pre-biomanipulation period to 50% of the lake surface area afterwards (Beklioglu et al., 2003; Beklioglu & Tan, 2008). However, in the dry years 2004 and 2005, Lake Eymir TP rose to levels comparable to those pre-biomanipulation, despite low external TP loading (fish biomass increased and macrophyte declined), followed by a new decline after the second biomanipulation in 2006.

For nitrogen, we only have information on dissolved inorganic N (DIN, nitrate and ammonium). In Lake Eymir, a sharp decrease in in-lake DIN followed the sewage effluent diversion. A fast response to external nitrogen loading reduction has been seen in many lakes (Jeppesen et al., 2005); reflecting low accumulation of N in the sediment compared to what is typical for phosphorus. However, fish removal likely contributed to the decline in DIN as seen in several whole-lake fish manipulation experiments in the north temperate zone (Jeppesen et al., 1998; Svensson et al., 1999). The role of fish biomanipulation seems supported by the decrease in in-lake DINs in Lake Eymir following the second event of fish removal (2006–2007) after years with higher DIN concentrations. It is evident that high macrophyte coverage was not associated with particularly low inorganic N in this lake. This contradicts results from north temperate freshwater lakes where submerged macrophytes enhance nitrogen removal by offering surfaces for nitrification and denitrification and by enhancing oxygen depletion during night, thereby stimulating denitrification in the sediment and on plant surfaces (Reddy & De Busk, 1985; Eighmy & Bishop, 1989; Eriksson & Weisner, 1997).

Notable is the higher ammonium and nitrate concentrations (and thus DIN concentrations) during the dry, warm years from 2001 and from 2003 and onwards in both lakes despite low external loading and even in years with high macrophyte coverage in Lake Eymir. While higher ammonium accumulation may be attributed in part to a lower oxygen concentration in the dry years it is somewhat surprising that nitrate is higher in dry years. It has often been argued that loss by denitrification is higher in warm lakes (Lewis, 1987), which should have resulted in lower concentrations in the warm dry years in the two lakes. In addition, the loss expectedly should have been amplified by the concurrent reduction in mean depth that at least for north temperate lakes often leads to increase in loss by denitrification (Windolf et al., 1996), likely as a result of enhanced contact between water and sediment. However, a recent lake climate gradient study of shallow lakes from the tropical to the cold regions in South America did not find nitrate concentrations to be particularly low in tropical lakes (Kosten et al., 2009). Actually, in their study high nitrate to ammonia ratios were found in several of the tropical lakes, indicating that denitrification was inefficient, possibly because of lack of high quality organic matter (Kosten et al., 2009). This was hardly the case in our two eutrophic lakes, which is supported by the fact that most of the nitrate entering the lakes was lost on an annual basis, thus nitrate entering during the winter season was lost during summer (Özen et al., unpublished data). Higher nitrate concentrations in the dry years are therefore an effect of evaporation rather than of a reduced capacity of denitrification. Reduced contact to the extensive reed zone around Lake Mogan (102 ha, or approx 15%) may have contributed to higher nitrate concentrations in dry years in this lake as Gökmen (2004) found a high water level to be important for efficient N retention in the reed beds surrounding the lake.

The higher TP and DIN concentrations in the dry years may have destabilised the clearwater state (Moss, 1990; Scheffer et al., 1993) in Lake Eymir, leading to disappearance of the submerged plants, though low water levels in dry years occasionally lead to higher macrophyte coverage (Gafny & Gasith, 1999; Havens et al., 2004; Beklioglu et al., 2006) or to no change in abundance (Özkan et al., 2010). In Lake Mogan, the coverage of submerged plants also decreased.

Our results show that the response of shallow lakes to changes in nutrient loading triggered by variations in hydraulic loading (also affected by climate) and also the effects of biomanipulation on nutrient retention and concentrations in shallow lakes differ from the expectations based on studies of cold temperate lakes (Jeppesen et al., 2009). The result is higher concentrations of both phosphorus and nitrogen in dry years, which enhances the risk of increased eutrophication sympthoms and thus higher turbidity of lakes. We can expect that drought events will occur more frequently in the future and with a higher intensity in semi-arid to arid Mediterranean lakes due to climate warming and changes in irrigation (Alcamo et al., 2007; Jeppesen et al., 2009). Lower critical nutrient loading levels for maintaining a clearwater state in shallow lakes are therefore to be expected in the arid zone in a future warmer and drier climate.



This study and AÖ were supported by a Middle East Technical University, BAP research grant, and the METU-DPT ÖYP programme of Turkey (BAP-08-11-DPT-2002-K120510), the EU projects EUROLIMPACS (www.eurolimpacs.ucl.ac.uk) and WISER (www.wiser.eu), by CLEAR (A Villum Kann Rasmussen Centre of Excellence project), The Research Council for Nature and Universe, Denmark (272-08-0406) and TUBITAK, BIDEB. We thank Anne Mette Poulsen for editorial assistance and Juana Jacobsen for technical assistance.


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Copyright information

© Springer Science+Business Media B.V. 2010

Authors and Affiliations

  1. 1.Limnology Laboratory, Biology DepartmentMiddle East Technical UniversityAnkaraTurkey
  2. 2.General Directorate of Electrical Power, Resource Survey and Development AdministrationAnkaraTurkey
  3. 3.Department of Freshwater Ecology, National Environmental Research InstituteAarhus UniversitySilkeborgDenmark

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