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Introduction
The Water Framework Directive (Directive 2000) led to the adjustment of existing assessment systems for water quality and encouraged the design of new classification systems for the ecological status of rivers. The new systems included new approaches to the definition of reference conditions (Pardo et al. 2011, 2012, 2018), the establishment of national and European river typologies, the definition of ecological status class boundaries, and the mandatory intercalibration of boundaries between European countries (Van de Bund 2009). Ecological status assessment has to be type-specific as streams have different biological communities and reference conditions due to their physical and morphological attributes, such as stream size, altitude, catchment geology, etc.
Benthic diatoms are one group of organisms widely used as ecological indicators in water quality and ecological status assessment and monitoring and are widely used as proxies for “phytobenthos” in WFD assessments. Many indices based on species-specific sensitivities and tolerances have been developed to infer the environmental conditions in streams and rivers. The WFD requires that methods are expressed as Ecological Quality Ratios (EQRs), defined as the “observed” (O) value of a metric divided by the value “expected” (E) at reference condition (O/E). In this study two diatom indices; IPS (Indice de polluo-sensibilite, CEMAGREF 1982), and TI (Trophic Index, Rott et al. 1999) were used to estimate ecological status in a small karstic river in Bosnia and Herzegovina (BH). It presents the relationship between measured water quality variables in the Bunica River and values of diatom indices. Two diatom metrics (IPS and TI) were compared and then combined into the phytobenthos Intercalibration Common Metric (pICM, Kelly et al. 2009).
Also, various diversity indices are used to determine the distribution of benthic diatoms. Diversity index is a statistical method which is planned to evaluate the variety of a data group consisting of different types of components. Number of existing species (richness), distribution of individuals equally (evenness) and total number of existing individuals underlie the basis of diversity indices. Three diversity indices (the Shannon Diversity Index, Simpson Diversity Index, Margalef Diversity Index) and one evenness index (Pielou’s Evenness Index) were used in this paper.
The purposes of this paper are: to present the list of benthic diatom assemblages; to assess the seasonal variations and ecological status of the river; to test the use of two diatom indices as tools for estimating the ecological status of small karstic rivers; and to explore the potential for using the pICM as a national metric for countries such as BH which are developing WFD-compatible phytobenthos methods at a relatively late stage.
Material and methods
Study area
The Bunica River is a limestone karstic river in the south of Bosnia and Herzegovina and is a tributary of the Buna River, itself part of the Neretva River basin (Fig. 1). In terms of geology and geomorphology the Bunica River is part of the Dinaric karst or Dinaric carbonate platform - external Dinarides (Milanović 2006). Thick layers of carbonate-formed long carbide precipitation characterize this area. The dominant clasts of the sediment are cobbles and sand. The siphon spring of the Bunica River is the underground extension of the flow of the Zalomka River (Fig. 1). The siphon is 73 m deep and ranks among the largest sources of the Dinaric karst (Milanović 2006). The minimum and maximum discharges registered for the Bunica Spring were 0.72 and 207 m3 s-1 (Milanović 2006). It is located in an area with a Mediterranean climate, characterized by long, hot summers and rainy winters with rare occurences of snow (Galić 2011). The average annual air temperature is 14.6 °C. The highest daily average temperature is 23.2 °C in July and the lowest below 5.8 °C in January (data for the city of Mostar, for the period 1971-2000, recorded by Meteorological and Hydrological Service of Bosnia and Herzegovina). The total annual precipitation is about 1515 mm. This area has approximately 2291 hours of sunshine per year. Average relative humidity is 69.
Fig. 1.Sampling sites marked with numbers 1, 2 and 3 along the studied Bunica River, tributary of the river Buna in Bosnia and Herzegovina.
So far, diatoms were studied only in the spring area of the Bunica River, revealing high diversity of taxa on artificial (glass slides) and natural substrates (Dedić 2015, Dedić et al. 2015).
Sampling and analyses
The ecological river typology in Bosnia and Herzegovina was developed according to System B of the WFD Annex II, which allows any natural environmental parameter-influencing communities to be included. A total of 216 water bodies of surface waters have been identified in the Adriatic Sea river basin district in the Federation of BH, specifically 211 running waters, four (4) stagnant waters and one (1) coastal water body (Mrđen et al. 2018). Within this typology the Bunica River belongs to type 12, subundertype 12a, small and medium lowland rivers on limestone sediment.
For this study, a total of 12 benthic diatom samples (three sampling locations: the source of the river, the middle course, and the lower course, each each once per season: spring - May, summer - July, autumn - October in 2013, and winter in January 2014) were collected by scraping the biofilm from rock surface, applying the the standard procedure of scraping sludgy material from the rock surface while making sure that the total surface of all rocks is about 500 cm2 (CEN 2003). The upper surface of each rock was scratched with a scalpel and carefully scrubbed with a toothbrush. The samples were fixed with 4% formaldehyde and stored in appropriately labelled bottles. In the laboratory, samples were treated with concentrated sulphuric acid, potassium-permanganate and oxalic acid (Krammer and Lange-Bertalot 1986). The cleaned suspension was used to make permanent diatom microscope slide preparations. The composition and relative abundance of diatoms were estimated at 1000× magnification, using a Carl Zeiss Jena light microscope. At least 400 valves were counted and identified. Identification and nomenclature were based on the relevant scientific literature and keys: Krammer and Lange-Bertalot (1986, 1988, 1991), Lange-Bertalot (2001), Krammer (2000-2003), Krammer and Lange-Bertalot (2004). The nomenclature of taxa follows AlgaeBase (Guiry and Guiry 2020).
Physico-chemical parameters (pH, electric conductivity (EC), dissolved oxygen (DO), oxygen saturation (SA) and temperature of water (T)) were measured at the same time that diatom samples were collected using a WTW probe (Wissenschaftliche-Technische Wersättem GmbH & Co. KG-Weilheim). Water samples were also taken and analysed by standard spectrophotometric methods in in the Laboratory of Public Health Mostar to current norms. The following chemical parameters were analyzed: dissolved oxygen (DO), chemical oxygen demand (COD), nitrate (NO3-), ammonium (NH4+), total nitrogen (TN), total phosphorus (TP), orthophosphate (PO43-) and silica (SiO2). Diatom indices were calculated using OMNIDIA GB 5.3 software (Lecointe et al. 1993). Indices taken into account for the assessment of water quality are those with the highest proportion of species used in the calculation. Values of indices in OMNIDIA software range from 1 to 20, indicating the quality range from polluted to clean water. The following indices were used: IPS (CEMAGREF 1982) and TI (Rott et al. 1999). We estimated diatom diversity using Shannon´s (H´), Simpson ´s (1-lambda), Margalef´s (d) diversity indices and Pielou´s Evenness Index (J). Indices were calculated with the PAST software (Hammer et al. 2001).
Chemical data were processed using principal component analysis (PCA) to obtain different water quality groups. The variables used in these analyses were pH, electrical conductivity, dissolved oxygen, oxygen saturation, water temperature, chemical oxygen demand, ammonium, nitrate, total nitrogen, total phosphorus, orthophosphate and silica.
Diatom data were analyzed using Primer v.6 (Clarke and Gorley, 2006): hierachical group average clustering, SIMPROF test, Principal Coordinates Analysis (PCO), to represent the distribution of the communities; SIMPER analysis (SIMilarity PERcentage) to estimate the degree of similarity within and among different groups (i.e., reference vs non-reference), and to estimate the individual contribution and the importance of each taxon to the global similarity among groups. These analyses were based on the Bray-Curtis similarity matrix which combines information on the relative abundance of species and faithfulness of the occurrence of species abundances in particular groups.
The phytobenthos Intercalibration Common Metric (pICM) was conceived by Kelly et al. (2009) as a means of converting national assessment metrics to a common scale. It is calculated as the average of EQRs (ecological quality ratios) computed using the Indice de Polluosensibilité Specifique (IPS, CEMAGREF 1982) and the Trophic Index (TI: Rott et al. 1999). The pICM is defined as the average of two EQRs: ICM = (EQRIPS + EQR TI)/2.
The pICM metric responds along a long gradient of inorganic and organic enrichment (Kelly et al. 2009, 2012). For this study we adopted the “expected” values of 16.8 (IPS) and 7.3 (TI) used for streams similar to the karstic streams in this study during the Mediterranean phytobenthos intercalibration exercise (Almeida et al. 2014). We also used the average position of the high/good and good/moderate ecological status class boundaries (0.9 and 0.69) established during this study as a starting point for understanding the ecological condition of these streams in comparison to others in the Mediterranean basin.
Both metrics were calculated using Omnidia version 5.3 (Lecointe et al. 1993) and converted to EQRs by dividing the observed value by the ‘expected’ value. The pICM was then transformed against national metrics and national EQRs for High/Good and Good/Moderate status boundaries converted to equivalent values of pICM.
Results
Physico-chemical and chemical variables per seasons
The main abiotic variables measured in the Bunica River are shown in Tab. 1. Nutrient concentrations are low, the water is well-oxygenated and pH is typical for water of carbonate bed/origin and generally oligotrophic conditions. Water quality corresponds to natural status without anthropogenic influence, following Anonymous (2014) and should support high ecological status.
| Parameter/ Station | Bunica 1 (n=4) | Bunica 2 (n=4) | Bunica 3 (n=4) | |||||||||
|---|---|---|---|---|---|---|---|---|---|---|---|---|
| Min. | Max. | Avg. | SD | Min. | Max. | Avg. | SD | Min. | Max. | Avg. | SD | |
| T (°C) | 11 | 14.2 | 12.8 | 1.4 | 11.4 | 15.5 | 13.7 | 1.7 | 11.4 | 17 | 14.6 | 2.3 |
| pH | 7.6 | 8 | 7.8 | 0.17 | 7.7 | 7.9 | 7.8 | 0.05 | 7.8 | 7.9 | 7.8 | 0.04 |
| EC (µS cm-1) | 313 | 403 | 372.5 | 40.4 | 314 | 406 | 371.5 | 39.8 | 312 | 406 | 369.2 | 40.3 |
| DO (mg L-1) | 9.65 | 12.25 | 11.28 | 1.16 | 11.2 | 12.7 | 11.88 | 0.66 | 11.43 | 13.3 | 12.2 | 0.84 |
| SA (%) | 90.1 | 119.3 | 106.9 | 13.4 | 90.1 | 127.9 | 107.2 | 15.6 | 103.4 | 132 | 120.8 | 12.3 |
| COD (mg L-1) | 0.77 | 1.28 | 1.02 | 0.23 | 1.02 | 3.58 | 2.07 | 1.17 | 0.89 | 2.43 | 1.47 | 0.66 |
| NH4+ (mg L-1) | 0 | 0 | 0 | 0 | 0 | 0.003 | 0.0007 | 0.0015 | 0 | 0.003 | 0.0007 | 0.001 |
| NO3- (mg L-1) | 0.18 | 0.45 | 0.35 | 0.12 | 0.29 | 0.49 | 0.37 | 0.08 | 0.27 | 0.43 | 0.36 | 0.067 |
| TN (mg L-1) | 0.30 | 0.61 | 0.47 | 0.13 | 0.37 | 0.55 | 0.47 | 0.07 | 0.37 | 0.52 | 0.45 | 0.062 |
| SiO2 (mg L-1) | 2.68 | 4.8 | 3.63 | 0.97 | 3.10 | 4.71 | 4.04 | 0.68 | 3.14 | 4.20 | 3.86 | 0.48 |
| TP (mg L-1) | 0.006 | 0.011 | 0.008 | 0.002 | 0.004 | 0.01 | 0.007 | 0.0009 | 0.006 | 0.008 | 0.0066 | 0.0009 |
| PO43- (mg L-1) | 0.002 | 0.005 | 0.0035 | 0.00 | 0.002 | 0.003 | 0.0026 | 0.0007 | 0 | 0.005 | 0.0018 | 5.13 |
Differences between sites along the Bunica River, and fluctuations among the seasons were not pronounced. Water temperature ranged from 11-17 °C (Tab. 1) and showed relatively low values for all the seasons. The lowest seasonal fluctuations were recorded at the spring. Dissolved oxygen concentration (9.65-13.3 mg L-1) and saturation (90.1-132%) (Tab. 1) were high at all sites and in all seasons. Conductivity ranged from 312 to 406 µS cm-1 (Tab. 1) with the lowest values in spring, and the highest in winter. All sites had slightly alkaline pH values (7.6 - 8) (Tab. 1). The most significant positive correlation was achieved among total nitrogen and silica (r = 0.9, P < 0.01), and negative correlation was found for total nitrogen and oxygen saturation (r = 0.677, P < 0.01). Multivariate analysis of the main chemical variables (PCA) in three dimensions accounted for 74.2% of the variance. The first three axes (PC1, PC2 and PC3) accounted for 45.4%, 18.9%, and 9.9% of the variance, respectively (Tab. 2). The most important parameters for the PCA axis 1 were TN and NO3-, with the coefficients in the linear combinations of variables of 0.400 for TN, and 0.374 for NO3-. The variables that weighted most for ordination for the PCA axis 2 were the COD and PO43- (coefficients in the linear combinations of variables: -0.477 and 0.432, respectively). The first axis differentiated spring and summer samples with low scores on PC1 from autumn and winter samples with high PC1 scores (Fig. 2).
| PCA | 1 | 2 | 3 | 4 | 5 |
|---|---|---|---|---|---|
| Eigenvalues | 5.44 | 2.27 | 1.19 | 1.04 | 0.872 |
| % variation | 45.4 | 18.9 | 9.9 | 8.7 | 7.3 |
| Cumulative % variation | 45.4 | 64.3 | 74.2 | 82.9 | 90.1 |
Fig. 2.Principal component analysis (PCA) ordination diagram performed on the environmental parameters for all sampling stations (1, 2, 3) in the Bunica River during four periods (a-spring, b-summer, c-autumn, d-winter) and overlapped with Pearson correlation vectors with PC1 and PC2 axes (r > 0.4). Abbreviations: EC – conductivity, T – temperature, NH4+ – ammonium, NO3- – nitrate, TN – total nitrogen, SiO2 – silica, PO43- – orthophosphate, TP – total phosphorus, COD – chemical oxygen demand, DO – dissolved oxygen, Sat. – oxygen saturation.
Analysis of benthic diatoms
In total, 147 diatom taxa from 43 genera were identified in the 12 samples from the Bunica River (Tab. 3). The genera with the highest number of taxa were Gomphonema (23 taxa), Navicula (18), Cymbella (10), Nitzschia (10) and Cocconeis (7). Meridion circulare (Greville) C.Agardh and Ulnaria ulna (Nitzsch) P.Comparé, recorded in all samples, followed by Cocconeis placentula Ehrenberg, C. euglypta (Ehrenberg) Grunow, C. lineata Ehrenberg, Diatoma vulgaris Bory de Saint-Vincent, D. vulgaris var. capitulata Grunow, D. vulgaris var. producta Grunow, Encyonema ventricosum (C.Agardh) Grunow, E. silesiacum (Bleisch) D.G. Mann, Gomphonema olivaceum (Hornemann) Brébisson, Melosira varians C.Agardh, Navicula tripunctata (O.F. Müller) Bory de Saint-Vincent, Rhoicosphenia abbreviata (C. Agardh) Lange-Bertalot and Navicula cryptocephala Kützing. All sampling stations had a similar species richness in all seasons. The number of taxa at Bunica 1 (spring area) ranged from 30 (in winter and summer) to 43 (in autumn), from 33 (spring) to 53 (autumn) for Bunica 2 (middle part of the river) and 40 (summer) to 49 (autumn) for Bunica 3 (the mouth of river). Values of Diversity and Evenness Indices per samples are shown in Tab. 4. Shannon’s Diversity Index ranged from 1.80 to 2.75, Simpson’s Diversity Index from 0.69 to 0.90, Margalef’s Diversity Index from 4.50 to 8.42 and Pielou’s Evenness Index from 0.20 to 0.41. The higest values of indices were recorded for the middle part of river (Bunica 2), mostly in summer (Tab. 4). The lowest values were in spring but for different locations (Tab. 4).
| Taxon | Max (%) |
|---|---|
| Achnanthes inflata (Kützing) Grunow | 8.33 |
| Achnanthes sp. | 83.33 |
| Achnanthidium minutissimum (Kützing) Czarnecki | 16.67 |
| Achnanthidium pyrenaicum (Hustedt) H.Kobayasi | 41.67 |
| Amphipleura pellucida (Kützing) Kützing | 8.33 |
| Amphora ovalis (Kützing) Kützing | 41.67 |
| Amphora pediculus (Kützing) Grunow | 58.33 |
| Amphora sp. | 8.33 |
| Aneumastus sp. | 8.33 |
| Aneumastus tuscula (Ehrenberg) D.G.Mann et A.J.Stickle | 25 |
| Aulacoseira italica (Ehrenberg) Simonsen | 41.67 |
| Brachysira microcephala (Grunow) Compère | 16.67 |
| Brebissonia lanceolata (C.Agardh) Mahoney et Reimer | 16.67 |
| Caloneis bacillum (Grunow) Cleve | 8.33 |
| Caloneis placentula Ehrenberg | 8.33 |
| Caloneis silicula (Ehrenberg) Cleve | 8.33 |
| Caloneis ventricosa var. truncatula (Grunow) Meister | 33.33 |
| Campylodiscus noricus Ehrenberg ex Kützing | 8.33 |
| Cocconeis euglypta Ehrenberg | 91.67 |
| Cocconeis lineata Ehrenberg | 91.67 |
| Cocconeis pediculus Ehrenberg | 66.67 |
| Cocconeis placentula Ehrenberg | 83.33 |
| Cocconeis placentula var. klinoraphis Geitler | 66.67 |
| Cocconeis pseudolineata (Geitler) Lange-Bertalot | 8.33 |
| Cocconeis robusta A. Jurilj | 25 |
| Cyclotella meneghiniana Kützing | 8.33 |
| Cyclotella sp. | 75 |
| Cymatopleura apiculata W. Smith | 8.33 |
| Cymatopleura elliptica (Brébisson) W. Smith | 25 |
| Cymbella affinis Kützing | 33.33 |
| Cymbella excisa Kützing | 8.33 |
| Cymbella excisiformis Krammer | 8.33 |
| Cymbella hungarica (Grunow) Pantocsek | 8.33 |
| Cymbella hustedtii var. crassipunctata Lange-Bertalot et Krammer | 8.33 |
| Cymbella laevis Nägeli | 25 |
| Cymbella parva (W.Smith) Kirchner | 16.67 |
| Cymbella parvula Krasske | 8.33 |
| Cymbella sp. | 16.67 |
| Cymbella subleptoceros Krammer | 16.67 |
| Denticula elegans Kützing | 8.33 |
| Denticula tenuis Kützing | 33.33 |
| Denticula tenuis var. crassula (Nägeli) Hustedt | 41.67 |
| Diatoma vulgaris Bory | 91.67 |
| Diatoma vulgaris var. capitulata Grunow | 83.33 |
| Diatoma vulgaris var. producta Grunow | 8.33 |
| Diploneis oblongella (Nägeli ex Kützing) A. Cleve | 25 |
| Ellerbeckia arenaria (Moore ex Ralfs) R.M.Crawford | 66.67 |
| Encyonema leibleinii (C. Agardh) W.J.Silva, R.Jahn, T.A.Veiga Ludwig et M.Menezes | 25 |
| Encyonema minutum (Hilse) D.G.Mann | 8.33 |
| Encyonema silesiacum (Bleisch) D.G.Mann | 66.67 |
| Encyonema ventricosum (C. Agardh) Grunow | 91.67 |
| Encyonopsis microcephala (Grunow) Krammer | 8.33 |
| Epithemia adnata var. saxonica (Kützing) R.M.Patrick | 8.33 |
| Epithemia muelleri Fricke | 25 |
| Epithemia sp. | 8.33 |
| Epithemia turgida (Ehrenberg) Kützing | 16.67 |
| Eunotia arcus Ehrenberg | 16.67 |
| Eunotia valida Hustedt | 8.33 |
| Fragilaria vaucheriae (Kützing) J.B.Petersen | 41.67 |
| Fragilaria recapitellata Lange-Bertalot et Metzeltin | 8.33 |
| Fragilaria sp. | 41.67 |
| Gomphonema acuminatum Ehrenberg | 33.33 |
| Gomphonema angustum C. Agardh | 33.33 |
| Gomphonema apicatum Ehrenberg | 8.33 |
| Gomphonema augur Ehrenberg | 41.67 |
| Gomphonema auritum A.Braun ex Kützing | 8.33 |
| Gomphonema calcareum Cleve | 25 |
| Gomphonema capitatum Ehrenberg | 8.33 |
| Gomphonema constrictum Ehrenberg | 8.33 |
| Gomphonema gracile Ehrenberg | 8.33 |
| Gomphonema grunowii R.M.Patrick et Reimer | 8.33 |
| Gomphonema micropus Kützing | 8.33 |
| Gomphonema minutum (C.Agardh) C.Agardh | 8.33 |
| Gomphonema montanum (J. Schumann) Grunow | 8.33 |
| Gomphonema olivaceum (Hornemann) Brébisson | 91.67 |
| Gomphonema parvulum (Kützing) Kützing | 16.67 |
| Gomphonema productum (Grunow) Lange-Bertalot et Reichardt | 8.33 |
| Gomphonema pseudoaugur Lange-Bertalot | 8.33 |
| Gomphonema pumilum (Grunow) E. Reichardt et Lange-Bertalot | 8.33 |
| Gomphonema sp. | 50 |
| Gomphonema subclavatum (Grunow) Grunow | 25 |
| Gomphonema tergestinum (Grunow) Fricke | 25 |
| Gomphonema truncatum Ehrenberg | 33.33 |
| Gyrosigma acuminatum (Kützing) Rabenhorst | 41.67 |
| Gyrosigma attenuatum (Kützing) Rabenhorst | 8.33 |
| Gyrosigma sciotoense (W.S.Sullivant) Cleve | 8.33 |
| Gyrosigma sp. | 16.67 |
| Halamphora veneta (Kützing) Levkov | 8.33 |
| Hantzschia amphioxys (Ehrenberg) Grunow | 25 |
| Iconella helvetica (Brun) Ruck et Nakov | 33.33 |
| Iconella linearis (W.Smith) Ruck et Nakov | 25 |
| Iconella spiralis (Kützing) E.C.Ruck et T.Nakov | 8.33 |
| Melosira sp. | 33.33 |
| Melosira varians C.Agardh | 91.67 |
| Meridion circulare (Greville) C.Agardh | 100 |
| Navicula amphibola Cleve | 8.33 |
| Navicula capitatoradiata H.Germain ex Gasse | 8.33 |
| Navicula cari Ehrenberg | 16.67 |
| Navicula cincta (Ehrenberg) Ralfs | 16.67 |
| Navicula cryptocephala Kützing | 75 |
| Navicula cryptonella Lange-Bertalot | 16.67 |
| Navicula jakovljevicii Hustedt | 16.67 |
| Navicula lanceolata Ehrenberg | 8.33 |
| Navicula microdigitoradiata Lange-Bertalot | 8.33 |
| Navicula oblonga (Kützing) Kützing | 25 |
| Navicula radiosa Kützing | 50 |
| Navicula reinhardtii (Grunow) Grunow | 50 |
| Navicula tripunctata (O.F.Müller) Bory de Saint-Vincent | 91.67 |
| Navicula trivialis Lange-Bertalot | 25 |
| Navicula veneta Kützing | 8.33 |
| Navicula viridula (Kützing) Ehenberg | 8.33 |
| Navicymbula pusilla (Grunow) K.Krammer | 8.33 |
| Navigeia decussis (Østrup) Bukhtiyarova | 8.33 |
| Neidium dubium (Ehenberg) Cleve | 8.33 |
| Nitzschia acicularis (Kützing) W.Smith | 16.67 |
| Nitzschia capitellata Hustedt | 8.33 |
| Nitzschia dissipata (Kützing) Rabenhorst | 8.33 |
| Nitzschia linearis W. Smith | 41.67 |
| Nitzschia palea (Kützing) W.Smith | 16.67 |
| Nitzschia pusilla Grunow | 8.33 |
| Nitzschia recta Hantzsch ex Rabenhorst | 8.33 |
| Nitzschia sigmoidea (Nitzsch) W.Smith | 33.33 |
| Nitzschia sp. | 41.67 |
| Nitzschia sublinearis Hustedt | 41.67 |
| Odontidium mesodon (Kützing) Kützing | 33.33 |
| Pinnularia microstauron (Ehrenberg) Cleve | 8.33 |
| Pinnularia sudetica Hilse | 16.67 |
| Pinnularia sp. | 8.33 |
| Placoneis gastrum (Ehrenberg) Mereschkovsky | 8.3 |
| Planothidium hauckianum (Grunow) Round et Bukhtiyarova | 8.33 |
| Planothidium lanceolatum (Brébisson ex Kützing) Lange-Bertalot | 25 |
| Reimeria sinuata (W. Gregory) Kociolek et Stoermer | 16.67 |
| Rhoicosphenia abbreviata (C. Agardh) Lange-Bertalot | 91.67 |
| Sellaphora bacillum (Ehrenberg) D.G.Mann | 41.67 |
| Sellaphora gregoryana (Cleve et Grunow) Metzeltin et Lange-Bertalot | 8.33 |
| Staurosira construens Ehrenberg | 8.33 |
| Staurosira venter (Ehrenberg) Cleve et Moeller | 16.67 |
| Staurosirella lapponica (Grunow) D.M.Williams et Round | 8.33 |
| Surirella angustata Kützing | 41.67 |
| Surirella grunowii Kulikovskiy, Lange-Bertalot et Witkovski | 16.67 |
| Surirella librile (Ehrenberg) Ehrenberg | 33.33 |
| Surirella minuta Brébisson ex Kützing | 8.33 |
| Tryblionella angustata W.Smith | 8.33 |
| Ulnaria acus (Kützing) Aboal | 8.33 |
| Ulnaria danica (Kützing) Compère et Bukhtiyarova | 41.67 |
| Ulnaria oxyrhynchus (Kützing) M.Aboal | 25 |
| Ulnaria ulna (Nitzsch) Compère | 100 |
| Station | Season | Sample code | H´ | 1-lambda | J | d |
|---|---|---|---|---|---|---|
| BUNICA 1 | spring | 1a | 1.94 | 0.71 | 0.24 | 4.50 |
| summer | 1b | 2.51 | 0.88 | 0.41 | 4.82 | |
| autumn | 1c | 2.17 | 0.80 | 0.20 | 6.94 | |
| winter | 1d | 1.88 | 0.69 | 0.21 | 4.82 | |
| BUNICA 2 | spring | 2a | 1.85 | 0.69 | 0.20 | 5.40 |
| summer | 2b | 2.75 | 0.91 | 0.41 | 6.15 | |
| autumn | 2c | 2.72 | 0.88 | 0.29 | 8.42 | |
| winter | 2d | 2.64 | 0.87 | 0.35 | 6.48 | |
| BUNICA 3 | spring | 3a | 2.44 | 0.85 | 0.25 | 7.27 |
| summer | 3b | 2.26 | 0.81 | 0.25 | 6.13 | |
| autumn | 3c | 2.40 | 0.81 | 0.22 | 8.09 | |
| winter | 3d | 2.11 | 0.77 | 0.20 | 6.45 |
SIMPER analyses showed high disimilarity among the seasons. The dissimilarities among the samples in different seasons ranged from 60.83% (spring-summer) to 70.24% (autumn-winter). The spring group showed 36.8% similarity, and was characterized by Melosira varians (MVAR), Diatoma vulgaris var. capitulata (DVCA), Meridion circulare (MCIR) and Gomphonema olivaceum (GOLI). The summer group showed 37.77% similarity, characterized by Encyonema ventricosum (EVEN), Navicula tripunctata (NTPT), and Cocconeis placentula (CPLA). Autumn samples showed the lowest similarity, 35%, with C. euglypta (CPLE), Achnanthes sp. (ACSP) and M. circulare (MCIR) as the most typical species. Winter samples had 35.9% similarity and were characterized by M. circulare (MCIR), Ellerbeckia arenaria (EARE) and C. placentula (CPLA). Similar results were obtained for the analysis of longitudinal gradient/locations with dissimilarities ranging from 64.79% between the first and second sites to 68.6%, between the second and third locations. However, similarity in species compostion was much higher between sampling periods at the first location of Bunica River (40.1%) than at the second (29%) or third (25.7) locations. The most abundant taxa at Bunica 1 were: E. ventricosum, E. silesiacum and Planothidium lanceolatum; at Bunica 2 Halamphora veneta, C. euglypta and C. placentula and at Bunica 3 G. olivaceum, Achnanthes sp. and C. placentula var. klinoraphis. Hierarchical group average clustering and the SIMPROF test followed by SIMPER analysis identified two groups and three ungrouped samples. Figure 3 shows the results of PCO analysis conducted using a Bray Curis similarity matrix and overlain with hierarchical clustering with vectors given by the Pearson correlation coefficient with environmental data and most significant taxa. The first group on the plot included all samples from location 1, except winter samples, summer and winter samples from location 2, and spring and winter samples from location 3. This group was characterized by G. olivaceum (GOLI), E. ventricosum (EVEN), and M. circulare (MCIR) up to 35% cumulative contribution and is associated with lower values of PO43-, consumption of chemical oxygen demand (COD) and electrical conductivity (EC). The second group is composed of autumn samples from the second and third location and was characterized by C. euglypta (CPLE) and C. placentula var. klinoraphis (CPLK) with up to 50% cumulative contribution; these samples are associated with higher values of SiO2 and NO3-. The ungrouped samples were 1d (dominated by P. lanceolata (ALAN) and C. placentula (CPLA), 2a with high abundance of Ulnaria oxyrhynchus (UOXY) and H. veneta (AVEN) and 3b, dominated by Cymbella laevis (CLAE) and Nitzschia pusilla (NIPU).
Fig. 3.Principal coordinates analysis (PCO) diagram comparing the community composition between samples in different seasons. PCO plot coded by the species vectors indicates taxa (A) and environmental vectors (B) positively correlated to PC1 and PC2 axes (r > 0.5; r > 0.3, respectively), and overlapped with the cluster groups based the 35% resemblance level of the group average clustering. Abbreviations: ACSP – Achnanthes sp., CPED – Cocconeis pediculus, CPLL – C. lineata, CPLK – C. placentula var. klinoraphis, CPLE – C. euglypta, MVAR – Melosira varians, EVEN – Encyonema ventricosum, ESIL – E. silesiacum, GOLI – Gomphonema olivaceum, MCIR – Meridion circulare, NRAD – Navicula radiosa, NTRI – N. tridentula, UULN – Ulnaria ulna; T – temperature, NH4+ – ammonium, SiO2 – silica, EC –conductivity, PO43- – orthophosphate.
Diatom indices
The data were used to calculate values of IPS and TI for all samples. IPS calculations used 95-100% of diatoms per sample whilst TI calculations used 65-95%. The values of indices for IPS ranged from 8.9 to 18.5 and for TI from 4.9 to 12.6. The two indices were not significantly correlated with each other or with measured physical and chemical parameters (P > 0.05). The pICM values ranged from 0.21 (2a) to 1 (2c) (Tab. 5), with mean values suggesting good status at Bunica 3 but not at the other two sites (based on an intercalibrated boundary value of 0.69). The concentrations of physical and chemical parameters should mean that the Bunica River can support high ecological status (Tab. 5), so the reason for this mismatch needs to be explored. Biotic index classes assigned by Omnidia showed variations in results from high to low ecological status. IPS values mostly in autumn season on all sites referred to the first category, while TI values mostly varied from fourth to fifth category, indicating extremely high trophic status (Tab. 5). However, these classes are over-simplistic and do not give nuanced insights into conditions in any particular river. The percentage of pollution tolerant taxa for site 1 were 0.3% in spring, 1.8% in summer, while for autumn and winter they were not registered. For site 2 there were 39.7 pollution tolerant taxa registered and for site 3 those taxa were not recorded.
| Station | Season | Sample code | IPS | TI | pICM | NH4+ | NO3- | TN | TP |
|---|---|---|---|---|---|---|---|---|---|
| BUNICA1 | spring | 1a | II | V | 0.57 | I | I | I | I |
| summer | 1b | I | V | 0.64 | I | I | I | I | |
| autumn | 1c | I | V | 0.77 | I | I | I | I | |
| winter | 1d | II | V | 0.47 | I | I | I | I | |
| BUNICA2 | spring | 2a | IV | V | 0.21 | I | I | I | I |
| summer | 2b | II | V | 0.61 | I | I | I | I | |
| autumn | 2c | I | III | 1 | I | I | I | I | |
| winter | 2d | II | V | 0.61 | I | I | I | I | |
| BUNICA3 | spring | 3a | I | V | 0.63 | I | I | I | I |
| summer | 3b | II | IV | 0.74 | I | I | I | I | |
| autumn | 3c | I | IV | 0.76 | I | I | I | I | |
| winter | 3d | I | V | 0.70 | I | I | I | I |
Discussion
In this paper the benthic diatom assemblages in karstic river in BH were studied in order to estimate ecological status and to test the future applicability of diatom indices. Benthic diatoms have been recommended in recent decades as appropriate tools for pollution assessment in rivers (e.g., Coste et al. 1991, Whitton and Kelly 1995), and have been used worldwide (Porter et al. 2008, Mangadze et al. 2015). Although our results indicate that the nutrient concentrations of the water do not determine the composition and structure of the benthic diatom assemblage in the Bunica River, this is likely to be due to the short gradient encountered during this study. All sites in all seasons had low nutrient concentrations and good oxygenation. The high oxygen saturation and water transparency, as well as low nutrient concentrations, indicate the oligotrophic character of the river. For the investigated stations in different seasons, no major seasonal fluctuations and differences in physical and chemical parameters were identified, which is probably due to the proximity and impact of springs along this short river (just 5.8 km in length). Water temperature (11-17 °C) showed relatively low values for all seasons. The smallest fluctuations were closest to the spring due to the temperature stability of spring water. High values of dissolved oxygen (9.65-13.3 mg L-1) and saturation (90.1-132%) are due to lower water temperature, porosity of the rock aquifer and contact between groundwater and the atmosphere (Cantonati 1998). Higher conductivity values indicate higher mineralization and our results suggest that the Bunica River has moderate mineralization. Physical and chemical values in this study are in accordance with values for limestone substrate (Mogna et al. 2015).
The analysis of the diatom assemblages revealed high species diversity. The investigated sites in the Bunica River were characterized by similar numbers of diatom taxa, and high species diversity indicates that there were favorable conditions for development. A similar number of diatom taxa (117) was recorded in the Mura River (Krivograd-Klemenčić and Balabanič 2010), while in the Bunica spring 104 (Dedić et al. 2015) and 87 (Hafner and Jasprica 2010) taxa were recorded. Although this is not universally applicable, similar correspondence between low levels of pollution and high species diversity were also observed by Noga et al. (2014). The Bunica River has a low level of organic pollution and it is not impacted by many anthropogenic stressors (high density of population, livestock farming, developed industry, etc.). This was also supported by diversity and evenness indices. Although values of indices varied for longitudinal and temporal patterns they indicated that the structure of habitats were stabile and balanced. Their variations reflect the heterogeneity of the diatom population. Those genera that were well represented in this study (Gomphonema, Navicula and Nitzchia) were also well represented in other studies of karstic rivers (Wojtal 2009, Dedić et al. 2015). All three genera are found across the whole range of the Bunica River, with particular species favouring different levels of ions and nutrients. Meridion circulare and Ulnaria ulna were recorded in all samples. Meridion circulare is a widespread, mesosaprobous and oligo to eutraphentic alkaliphilous diatom (Van Dam et al. 1994). Ulnaria ulna occurs in oligo- to polytrophic and oligo-saprobic to α-mesosaprobic waters (Hofmann et al. 2013) and is also classified as alkaliphilous (Van Dam et al. 1994). The occurence of large numbers Halamphora veneta in a spring at the middle location is, however, very unusual. It occurs in fresh and slightly brackish water. According to Van Dam et al. (1994) it is an alpha/polisaprobic and eutrophic taxa.
Taxa of the genera Amphora, Cocconeis and Diatoma, frequently found in this research, have a high indicator values for pH, organic nitrogen, oxygen, saprobity and trophic state (Van Dam et al. 1994). Diatoms are influenced by many factors including those that are site-specific on various temporal and species scales (DeNicola et al. 2004) as well as those that reflect human interventions in the environment. Those factors include chemical properties of the water (Potapova 1996), nutrient load (Rott et al. 1997) and also flow velocity and substratum type (Rimet 2009). The results of this study showed that physical and chemical variables and seasons did not have a notable effect on the diversity of benthic diatoms in the Bunica River. It is possible that hydromorphological and other water conditions such as flow velocity, type of substrates, discharge of water, marginal vegetation in karstic river also influenced the structure and composition of benthic diatom assemblages more than physical and chemical variables.
IPS and TI did not always give consistent results along the entire length of the Bunica River. One important reason is that they were developed for different purposes – IPS measures “general degradation” whilst TI was developed, specifically, to measure the impact of inorganic nutrients. IPS index showed better water quality along the entire length of the Bunica river (mostly moderate, II and III class) compared with the TI trophic index, which indicated a poor or bad ecological status of the river (IV-V class). This variation has also been noted by others, Kitner and Poulícková (2003), Poulíčková et al. (2004), and Stenger-Kovács et al. (2007), Szczepocka and Szulc (2009), Kalyoncu and Şerbetci (2013). Because the indices were developed for different purposes, naive division of the scale into equal-sized segments, though an easy option (e.g., Eloranta and Soininen 2002), is unlikely to give meaningful results or consistency between indices. Others have noted that indices developed in certain regions of Europe were not effective in others (Pipp 2002, Rott et al. 2003).
Our study also noted a mismatch between status assessment using the average pICM boundary set during the Mediterranean intercalibration exercise (Almeida et al. 2014) and observations in this study. The nature of the Bunica River is such that we should estimate high or good status based on diatom assemblages, whereas our results indicate less than good status at two of the sites. Kamberović et al. (2019 a) used TI index in a study of springs on Konjuh Mountain (BH) and reached similar conclusions about the suitability of existing indices, recommending some modifications to the TI. Our study has also identified potential mismatches between ecological status boundaries used elsewhere in the Mediterranean basin and those used in BH, suggesting a need to recalibrate the pICM, if it is to be used successfully here. Based on this study, we recommend “expected” values for pICM calculations of 16.8 and 7.3 for IPS and TI, respectively.
Diatom indices have been shown to be one of the most effective tools for evaluating ecological status in European rivers (Eloranta and Soininen 2002, Kelly et al. 2008); however, further testing of IPS and TI diatom indices was needed to ensure their utility in small karstic rivers in BH. The suitability of indices depends, to some extent, on the percentage of taxa used for index calculation. In this study 95-100% of taxa were used for the IPS calculation, suggesting that it is highly suitable. For the TI, a smaller percentage was used (60-90%). In the study of epiphytic diatoms in Lake Modrac in northeastern BH, Kamberović et al. (2019b) also concluded that the IPS and TI were most suitable. However, consideration should also be given to how sensitivity values are assigned to taxa and, in this respect, the IPS does not have a transparent process for determining such scores whilst the TI has never been updated since first published (Rott et al. 1999). On the other hand, both are widely used around Europe (Poikane et al. 2016) and, therefore provide a means by which results from BH can be compared with data from other countries. Rather than develop a new index, therefore, we have adopted the ‘‘phytobenthos Intercalibration Common Metric’’ (pICM, Kelly et al. 2009), based on these two metrics, as an interim tool for evaluating ecological status using phytobenthos in BH. These values are similar to those proposed for Mediterranean streams by Kelly et al. (2012), and higher similarities were recorded in IPS than in TI, but have the benefit for being more closely tuned to local conditions within BiH.
Conclusions
The Bunica River has a high diversity of benthic diatom taxa (147). Physical and chemical analyses indicated oligotrophic conditions in all locations and high ecological status. Measured physical and chemical parameters and seasons did not have a notable effect on the biological diversity of benthic diatoms. It is possible that hydromorphological and other water conditions such as flow velocity, type of substrates, discharge of water, marginal vegetation had a greater influence on structure and composition of benthic diatom taxa than physical and chemical variables. The diatom indices IPS and TI were used in our study and we concluded that combining them into the “phytobenthos Intercalibration Common Metric’’ (pICM) gave us more results that were more easily compared with those from elsewhere in Europe than would have been the case if only a single index had been used. We therefore recommend pICM as a good starting point for ecological status assessment in BiH and propose it as a potential national metric for phytobenthos assessment in the future. However, testing on a larger number of sites and along a longer gradient of ecological quality is necessary before this can be confirmed.
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Main Article Content
Abstract
The aims of this paper were to describe seasonal changes in the qualitative and quantitative composition of diatom taxa and the potential application of benthic diatoms for ecological status evaluation. Diatom indices (IPS and TI) were calculated from data from three different locations along a longitudinal profile of the Bunica, a small karstic river in Bosnia and Herzegovina. A total of 147 taxa were recorded in 12 samples. The most common taxa were Meridion circulare (Greville) C.Agardh and Ulnaria ulna (Nitzsch) Compère. Physical and chemical analyses showed low concentrations of nutrients, good oxygenation, typical pH for carbonate bed/origin and generally oligotrophic conditions and high ecological status. All sites had similar physico-chemical conditions and there were only few seasonal differences. Ordination of the diatom data showed that samples showed neither longitudinal nor seasonal patterns. Median value for IPS (16.8) and for TI (7.3) can be possible ‘‘expected’’ values for ecological status assessment for small karstic rivers in the Mediterranean region. We propose the use of the phytobenthos Intercalibration Common Metric (pICM - an index that combines the IPS and TI) as a national metric for countries developing WFD diatom methods at a late stage. One situation is described, and a solution, which is potentially transferable to other locations in Bosnia and Herzegovina and also to other countries facing similar challenges.
Keywords
Article Details
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