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Ukrainian Journal of Ecology
Ukrainian Journal of Ecology, 2020, 10(2), 455-460, doi:10.15421/220_123
ORIGINAL ARTICLE
Change of water properties during the process of floodplain
vegetation destruction
M.S. Bobrova1, R.M. Manasypov1, V.Yu. Shuvarikova1, A.S. Prokushkin2, E. Lutova1, L.P. Borilo1, E.S. Rabtsevich1, O.S. Pokrovsky3, L.F. Shepeleva1, I.V. Luschaeva1,
L.G. Kolesnichenko1*
1 Tomsk State University, Lenin Ave. 36, building 13, 634050, Tomsk, Russia 2Sukachev Institute of Forest SB RAS, Federal Research Center "Krasnoyarsk Science Center SB
RASKrasnoyarsk, Russia" 3GéosciencesEnvironnement Toulouse, UMR5563, IRD UR234, Université PaulSabatier, 14Avenue
EdouardBelin, Toulouse, France
Corresponding author E-mail: klg77777@mail. ru * Received: 10.05.2020. Accepted:28.06.2020
The destruction of plant residues of floodplain vegetation in the aquatic environment was studied. The objects of study were three herbsspecies dominant in the Ob floodplain: Inula salicina, Calamagrostis purpurea and Carex atherodes. Dissolved organic matter (DOM), which plays a significant role in the aqueous environment, was studied carefully. As a result of the work, there was revealed the species specificity in the leaching processes of major elements,trace elements and organic matterfrom herbs. It has been established that the motley grasses samples are primarily affected by the destruction process. The growth of dissolved organic carbon, aromatic substances, condensed carbon fragments in the structure of DOC components in the studied waters was observed in the first fifty hours of the experiment, then the corresponding indicators decreased, probably due to the mineralization of organic substances. Key words: destruction, flood, water properties, dissolved organic matter.
Introduction
The Ob floodplain landscape soccupy a significant part of the territory of Western Siberia and play a special role in the carbon cycle as the richest habitats (Vorobyev et al., 2019). Compared to non-floodplain spaces, these territories are better provided with moisture, heat, and mineral nutrition. However, until now, the studies of the Ob floodplain were mostly devoted to production processes in these territories (Shepeleva, 2018), while the process of degradation of floodplain vegetation during the spring flood remains extremely poorly studied. Meanwhile, significant attention is currently being paid to biological and photolytic degradation in the world (Moran, Zepp, 1997; Hansen et al., 2016).
We studied the destruction of plant residues of floodplain vegetation in laboratory conditions; special emphasis was put on dissolved organic matter (DOM). DOM plays a significant role in the aquatic environment, providing energy to the biota, redistributing light in the water column, interacting with mineral compounds (Minor et al., 2014; Hansen et al., 2016).
Nowadays researchers consider not only the total content of organic material but also its composition that determines its position in the environment (Liang and Singer, 2003; Minor et al., 2014). The research of the composition of dissolved organic carbon in water bodies focuses on a large number of works (Smith et al., 2004, Drozdova et al., 2019, Ilina et al., 2014), which contribute significantly to the understanding of the mechanisms of ecosystem sustainability and the carbon cycle of surface waters (Drozdova et al., 2019). Optical measurements of absorbance and fluorescence are increasingly used to track DOM (Coble, 2007; Fellman et al., 2010; Gabor et al., 2014). Most often, the indicator SUVA254 is used to assess the content of dissolved aromatic substances in waters, hydrophilicity and hydrophobicity, as well as the reactivity of DOC when interacting with coagulants and inorganic substances (Randtke, 1999; McKnight et al., 1992; Hoch et al., 2000; Weishaar, 2003). The higher is this indicator, the more aromatic substances are contained in natural waters.If the value of this coefficient is lower than 1, then low molecular weight aliphatic compounds will prevail in the waters (Weishaar et al, 2003; Chowdhury, 2013). A spectral coefficient E250:E365 is calculated to estimate the molecular weight, the content of condensed carbon fragments in the structure of the components of the DOM, and the ratio of the content of unoxidized aromatic structures to oxidized ones (Korshin et al, 1997; Peuravouri, Pihlaja, 1997). A spectral coefficient E254/E436 is calculated to assess predominance of autochthonous or allochthonous DOM (Battin, 1998; Jaffé et al., 2004; Hur et al., 2006; Ilina et al., 2014). The wavelength ratio
E400:E600 is calculated to understand the degree of humification of DOM and O:C and C:N atom ratio (Chin et al., 1994; Stevenson, 1994; Hur et al., 2006).
Materials and methods
The objects of there search were thre eplants species dominant in the Ob floodplain: Inula salicina, Calamagrostis purpurea and ,which were collected near the Kaibasovo research station of Tomsk State University. Work was conducted with the application of equipment of the large-scale research facilities «System of experimental bases located along the latitudinal gradient» (http://ckp-rf.ru/usu/586718/).
Prior to the experiment, plant samples were dried in an oven at a temperature of 45 °C for 36 hours to an air-dry state; then the samples were weighed under laboratory conditions. The weighed and dried plants were mixed in sterile glass containers of 1 litre with the addition of distilled water.
The containers were stored for 200 hours in a thermostat at a constant temperature of 20 °C. Measurements of pH and electrical conductivity were performed at specified intervals by Multi 3400i liquid analyzer. The collected water samples were filtered through 0.45 pm filters. The elemental composition was determined at the Tomsk Regional Center for Collective Use Tomsk State University using the ICP-MS method with the help of Agilent 7500 cx.
The research of the dissolved organic carbon (DOC), the dissolved inorganic carbon (DIC) and the structure of organic matter of tests were conducted on the basis of Forestry Institute of V.N. Sukachyov of the Siberian Branch of the Russian Academy of Science in Krasnoyarsk with use of the analyzer TOC minicube and the spectrophotometer Varian 100 UV-Vi. From the absorption spectra of water samples in the ultra-violet and visible field, the followingvalues characterizing DOM were calculated, namely SUVA254, E250:E365, E465:E665, E254:E436.The SUVA254 value was calculated as the 254 nm absorption ratio (mg-1 m- 1) to the DOC content of the sample. We used statistical packages of the program "Statistica 6.0" to process the obtained results.
Results and discussion
Substances leached from plants entered to water, which electrical conductivity naturally increased during the experiment.The maximum electrical conductivity was observed during the destruction of plant residues of motley grass samples - Inula salicina, which may be associated with the highest leaching of major elements during the decomposition of this species.The minimum conductivity was noticed for samples of cereals - Calamagrostis purpurea (Fig. 1a). During the 220 hours of leaching, plant residues lost from 11 to 30% of the mass, with the maximum losses observed for Inula salicinaand the minimum for Calamagrostis purpurea. The pH of water in the first 30 hours after the start of the experiment sharply decreased in all cases (most of all, in the case with Carex atherodes), but then it began to increase and, starting from the hundredth hour of the experiment, a slight alkalization was observed in the water (Fig. 1 b).
500 -1- 7.5
0 -1-1-1-1- 5 -1-1-1-1-
0 50 100 150 200 250 0 50 100 150 200 250
Time' h Time, h
Fig. 1. Change of physicochemical characteristics. A - Conductivity, B - pH
Having studied the elemental composition of water after the experiment completion, it was established that potassium is most leached.The possible reason is that its content in the plant matter of this species is maximum (Table 1). The fact that the potassium content in herbaceous plants is usually higher than the content of other elements has been confirmed by some researchers (Covda, 1956; Archegova, 2011). Also, it is known that potassium is not a part of organic substances of plant cells, but is in free ionic form (Archegova, 2011).
Table 1. Potassium content in plants and water after the experiment, ppm
Plant species Inula salicina Carex atherodes Calamagrostis purpurea
Potassium content in plants 30836.10 18257.39 21485.45
Potassium content in water after the experiment_217.55_138.75_122.95_
For all the plants studied, the migration activity of macronutrients declining in the K >Ca> Mg > Na range. The maximum leachin of these major elements was noted for Inula salicina, the minimum for Calamagrostis purpurea (Fig. 2).
Species specificity was revealed in processes of leaching trace elements from plants. Thus, with the destruction of Inula salicina, Si and Rb were most actively introduced into the water, and then the entry activity decreased in the range Fe > B >Mn>Sr> Al > Zn > Ba > Cu > Ni > Se > Li. For Carexatherodes, this series is as follows: Si > Fe >Mn>Rb> Zn >Sr> Al > B > Ba > Cu > Ni > Se > Mo. The entry activity of trace elements for Calamagrostis purpurea destruction was represented by the following descending range: Mn> Si >Rb> Zn > Fe > Al > B >Sr> Ba > Cu > Ni > Se > V.
We have to note that trace elements entered the water in other ratios than these substances are found in plants; for example, the following series is characteristic of Carex atherodes plants: Si > Fe > Al >Mn> Ba >Rb> Zn >Sr> Ni > Cu > Ti > B > Cr >Sc> Mo; for plants Calamagrostis purpurea: Mn> Fe> Al> B> Si> Zn> Ti>Rb>Sr> Ba> Ni> Cu>Sr>Sn> Mo; Inula salicina: Fe>Rb>Sr>Mn> B> Si> Ba> Zn> Ni> Ti> Cu> Li> Cr. The largest number of major and trace elements passed into the water during the leaching of Inula salicina.
For the same plant species, the sharpest increase in conductivity and DIC content was noted. For all plant species, the dynamics of DIC entry into the water was close to the dynamics of electrical conductivity change (Fig. 3a), and the relationship between the increased conductivity and the content of major elements in water was also noted.
The dynamics of the intake of dissolved organic carbon is shown in Fig. 3b; it can be noted that a greater amount of DOC was released into the water during the leaching of Inula salicina than when other types of plants were leached. A particularly large amount of DOC in waters was revealed during the first hours of the experiment.
1,0 0,8 0,6 0,4 0,2 0,0
0,28
^ ^ 0,17 0,16 0,16
0,07 0,07 0,06 0,05 003 „„„
0,03 0,02 0,01 0,01 __■ ■__
Si Fe Mn Rb Zn Sr Al B Ba Cu Ni Se Mo
0,9 0,8 0,7 0,6 0,5 0,4 0,3 0,2 0,1 0,0
0,79
C D
0,28
0,17 0,16 0,16
0,07 0,07 0,06 0,05
0,03 0,02 0,01 0,01
Si Fe Mn Rb Zn Sr Al B Ba Cu Ni Se Mo
1,6 1,4 1,2 1,0 0,8 0,6 0,4 0,2 0,0
1,22
0,22 0,20
0,08 0,06 0,06 0,04 0,03 0,03 0,02 0,01 0,01
Mn Si Rb Zn Fe Al B Sr Ba Cu Ni Se V
1,35
Fig. 2. Amount of enleached major and trase elements, ppm. A - major elements; B - trace elementsin the process of leaching Inula salicina C - trace elements in the process of leaching Carex atherodes D - trace elements in the process of leaching Calamagrostis purpurea
0 50 100 150 200 250 0 50 100 150 200 250
Time, h Time, h
A B
Fig. 3. Dynamics of DIC (A) and DOC (B) content in water during plant enleaching
As can be seen, when the studied plant species were leached, the hydrophilic material fell into the water, as is indicated by the low SUVA254 (Sedzwald and Tobiason, 1999; Minor and Stephens, 2008; Matilainen et al., 2011). In the first hours of the experiment, the little amount of aromatics was present in the water, but then it increased sharply; this is especially characteristic of Inula salicina. The maximum of aromatic substances was noted in the waters at the fiftieth hour of the experiment, however, during the mineralization of substances, their amount decreases and after 200 hours this parameter is close to the initial values for all plant species (Fig. 4). After 120 hours of leaching Calamagrostis purpurea and Carex atherodes, the SUVA254 falls below 1, indicating that waters were dominated by only aliphatic compounds with low molecular weight (Weishaar et al., 2003; Chowdhury, 2013).
The spectral coefficient ofE250:E36sis also related to the molecular weight and content of condensed carbon fragments in the structure of the components of DOC (Korshin et al., 1997; Peuravouri, Pihlaja, 1997).It is believed that if the size of the molecules is larger, the E250:E365 ratiois smaller due to the stronger absorption of light by high molecular weight DOM on longer waves (Korshin et al, 1997). In our case, the lowest content of condensed carbon fragments was noted in the first hours of the experiment, then, within 50 hours, it grew, and then again decreased as well as the SUVA254indicator.
The E465:E665ratio correlates better with the size ratios of the molecules O:C and C:N and the content of carboxyl groups than with aromaticity and can, therefore, be used as a common feature of humification (Adani et al., 2006; Schnitzer et al., 1985; Chen et al., 1977). The values of the E465:E665 coefficient in the tested samples ranged from 1.9 to 13.3. The lowest E465:E665 values were found for Inula salicina and indicate a higher degree of humification of organic matter (Schnitzer et al., 1985; Chen et al., 1977).
Fig. 4. Changing the structure of organic matter during enleaching of floodplain plants. A -
D - E254:E436
SUVA254, B - E250:E365, C - E465:E665,
The values of the E254Î436 coefficient ranged from 7.37 to 50.4, with the maximum values being noted during the leaching of Inula salicina (Fig. 4d). In the first hours of the experiment, an autochthonous organic substance formed as a result of the life of microorganisms prevailed, then the spectral coefficient of E254Î436 decreased sharply and remained at a close level for all leached plants until the experiment completion. This suggests the inclusion in DOC of allochthonous substances originating from products of incomplete degradation of plant and animal residues (Ilina et al., 2014; Wang et al., 2001).
Conclusion
Therefore, species specificity was revealed in the leaching processes of major and trace elements and organic matter from plants. It has been established that samples of motley grass are primarily affected by the destruction process. The growth of dissolved organic carbon, aromatic substances and condensed carbon fragments in the structure of the DOC components in the investigated waters was observed in the first fifty hours of the experiment; then the corresponding values were reduced, probably due to the mineralization of organic substances. When the studied plant species were leached, hydrophilic material (aliphatic compounds with low molecular weight) fell into the water.
Acknowledgments
This research was supported by the RF Federal Target Program, project RFMEFI58717X0036.
References
Adani, F., Ricca, G., Tambone, F., Genevini, P. (2006). Isolation of the stable fraction, the core of the humic acid. Chemosphere,
65 (8), 1300-1307.doi:10.1016/j.chemosphere.2006.04.032 Archegova, I.B. (2011). The influence of woody plants on the chemical composition of precipitation during the restoration of
mid-taiga forests. Forest Science, 3, 34-43. [In Russian] Battin, T.J., (1998). Dissolved organic materials and its optical properties in a blackwater tributary of the upper Orinoco River,
Venezuela. Organic Geochemistry, 28, 561 -569.doi:10.1016/j.orggeochem.2013.10.008 Chen, Y., Senesi, N., Schnitzer, M. (1977). Information provided on humic substances by E4/E6 ratios. Soil Sci. Soc. Am, 41, 352 Chin, Y.-P., Aiken, G., O'Loughlin, E., (1994). Molecular weight, polydispersity, and spectroscopic properties of aquatic humic
substances. Environmental Science & Technology, 28, 1853-1858. doi:10.1021 /es00060a015 Chowdhury, S. (2013). Trihalomethanes in drinking water: Effect of natural organic matter distribution. Water SA, 39, 1 -7. Doi:10.4314/wsa.v39i1.1
Coble, P.G. (2007). Marine optical biogeochemistry: The chemistry of ocean color. Chem. Rev., 107, 402-18.doi:10.1021/cr050350
Drozdova, O. Yu., Ilyina, S.M., Anokhin, N.A., Zavgorodnaya, Yu.A., Demin, V.V., Lapitsky, S.A. (2019). Transformation of organic
substances in the conjugate series of surface waters of northern Karelia. Water resources, 46, 43-50 [In Russian] Fellman, J.B., Hood, E., Spencer, R.G.M. (2010). Fluorescence spectroscopy opens new windows into dissolved organic matter
dynamics in freshwater ecosystems: A review. Limnol.Oceanogr., 55, 2452-2462. doi:10.4319/o.2010.55.6.2452 Gabor, R.S., Baker, A., McKnight, D.M., Miller, M.P. (2014). Fluorescence indices and their interpretation. In: P. Coble, J. Lead, A.
Baker, D. Reynolds, and R.G.M. Spencer (Eds.). Aquatic organic matter fluorescence. Cambridge Univ. Press, 303-338 Hansen, A.M., Kraus, T.E.C., Pellerin, B.A., Fleck, J.A.,Downing, B.D., Bergamaschi B.A. (2016). Optical properties of dissolved
organic matter (DOM): Effects of biological and photolytic degradation. Limnol.Oceanogr, 61, 1015-1032 Hoch, A.R., Reddy, M.M., Aiken, G.R. (2000). Calcite crystal growth inhibition by humic substances with emphasis on
hydrophobic acids from the Florida Everglades.Geochim.Cosmochim. Acta, 6, 61 -72. Hur, J., Williams, M.A., Schlautman, M.A. (2006). Evaluating spectroscopic and chromatographic techniques to resolve dissolved organic matter via end member mixing analysis. Chemosphere, 63, 387-402. doi:10.1016/j.chemosphere.2005.08.069 Ilina, S.M., Drozdova, O.Yu., Lapitskiy, S.A., Alekhin, Yu.V., Demin, V.V., Zavgorodnyaya, Yu.A., Shirokova, L.S., Viers, J., Pokrovsky, O.S. (2014). Size fractionation and optical properties of dissolved organic matter in the continuum soil solution-bog-river and terminal lake of a boreal watershed. Organic Geochemistry, 66, 14-24 Jaffe, R., Boyer, J.N., Lu, X., Maie, N., Yang, C., Scully, N.M., Mock, S. (2004). Source characterization of dissolved organic matter
in a subtropical mangrovedominated estuary by fluorescence analysis. Marine Chemistry, 84, 195-210. Korshin, G.V., Li, C.W., Benjamin, M.M. (1997). Monitoring the properties of natural organic matter through UV spectroscopy: A
consistent theory. Water Research, 31 (7), 1787-1795 Kovda, V.A. (1956). Mineral composition of plants and soil formation. Eurasia soilscience, 1, 6-39. [In Russian] Liang, L., Singer, P.C. (2003). Factors influencing the formation and relative distribution of haloacetic acids and
trihalomethanes in drinking water. Environ. Sci. Technol. 37, 2920-2928. doi:10.1021 /es026230q McKnight, D.M., Bencala, K.E., Zellweger, G.W., Aiken, G.R., Feder, G.L., Thorn, K.A. (1992). Sorption of dissolved organic carbon (including fulvic and hydrophilic acids) by hydrous aluminium and iron oxides: A study of processes occurring at the confluence of Deer Creek with the Snake River, Summit County, Colorado. Environ. Sci. Technol. 2, 1388-1396. Minor, E.C., Swenson, M.M., Mattson, B.M., Oyler, A.R. (2014). Structural characterization of dissolved DOM optical properties following degradationorganic matter: A review of current techniques for isolation and analysis. Environ. Sci. Process. Impacts, 16, 2064-2079. doi:10.1039/C4EM00062E Moran, M.A., Zepp, R.G. (1997). Role of photoreactions in the formation of biologically labile compounds from dissolved
organic matter. Limnol.Oceanogr., 42, 1307-1316. doi:10.4319/lo.1997.42.6.1307 Peuravouri, J., Pihlaja, K (1997). Molecular size distribution and spectroscopic properties of aquatic humic 10 substances. Anal. Chim. Acta, 337, 133-149
Randtke, S.J. (1999). Disinfection By-Product Precursor Removal by Coagulation and Precipitive Softening. In: Formationand Control of Disinfection By-Products in Drinking Water; Singer, P.C. (Ed.). American Water Works Association: Denver, CO. Chapter 12, pp. 237-258.
Repeta, D.J., Quan, T.M., Aluwihare, L.I., Accardi, A.M., (2002). Chemical characterization of high molecular weight dissolved
organic matter in fresh and marine waters. Geochim.Cosmochim. Acta, 66, 955-962. doi:10.1016/S0016-7037(01 )00830-4 Schnitzer, M., Calderon, G. (1985). Somechemical characteristics of paleosolhumicacids. Chem. Geol, 53(3-4), 175-184. Shepeleva, L.F. (2018). Structure and dynamics of meadow communities in the floodplain of the Middle Ob. Tomsk University [In Russian]
Smith, R.E.H., Allen, C.D., Charlton, M. (2004). Dissolved Organic Matter and Ultraviolet Radiation Penetration in the Laurentian Great Lakes and Tributary Waters. Journal of Great Lakes Research, 30(3), 367-380. Doi: 10.1016/S0380-1330(04)70354-8
Stepanauskas, R., Moran, M.A., Bergamaschi, M.A., Hollibaugh, J.T. (2005). Sources, bioavailability, and photoreactivity of dissolved organic carbon in the Sacramento-San Joaquin River Delta. Biogeochemistry, 74, 131-149. doi:10.1007/s10533-004-3361 -2
Stevenson, F.J. (1994). Humus chemistry.Genesis, composition, reactions. N.Y.: John Wiley & Sons.
Vergnoux, A., Di Rocco, R., Domeizel, M., Guiliano, M., Doumenq, P., Theraulaz, F. (2011). Effects of forest fires on water extractable organic matter and hu-mic substances from Mediterranean soils: UV-vis and fluorescence spectros-copy approaches, Geoderma, 160 (3-4), 434-443. doi: 10.1016/j.geoderma.2010.10.014
Vorobyev, S.N., Pokrovsky, O.S., Kolesnichenko, L.G., Manasypov, R.M., Shirokova, L.S., Karlsson, J., Kirpotin, S.N. (2019). Biogeochemistry of dissolved carbon, major, and trace elements during spring flood periods on the Ob River. Hydrological Processes, 33 (11), 1579-1594. doi:10.1002/hyp.13424
Wang, G.S., Liao, C.H., Wu, F.J. (2001). Photodegradation of humic acids in the presence of hydrogen peroxide. Chemosphere, 42, 379-387
Weishaar, J.L, Aiken, G.R., Bergamaschi, B.A., Fram, M.S., Fujii, R., Mopper, K. (2003). Evaluation of Specific Ultraviolet Absorbance as an Indicator of the Chemical Composition and Reactivity of Dissolved Organic Carbon. Environ. Sci. Technol, 37, 4702-4708. doi:10.1021 /es030360x
Wetzel, R.G., Hatcher, P.G., Bianchi, T.S. (1995). Natural photolysis by ultraviolet irradiance of recalcitrant dissolved organic matter to simple substrates for rapid bacterial metabolism. Limnol. Oceanogr., 40, 1369-1380. doi:10.4319/lo.1995.40.8.1369
Yan, M., Dryer, D., Korshin, G.V. (2016). Spectroscopic characterization of changes of DOM deprotonation-protonation properties in water treatment processes, Chemosphere, 148(4), 426-435. doi: 10.1016/j.chemo-sphere.2016.01.055
Citation:
Bobrova, M.S., Manasypov, R.M., Shuvarikova, V.Yu., Prokushkin, A.S., Lutova, E.., Borilo, L.P., Rabtsevich, E.S., Pokrovsky, O.S., Shepeleva, L.F., Luschaeva, I.V., Kolesnichenko, L.G. (2020). Change of water properties during the process of floodplain
vegetation destruction. Ukrainian Journal of Ecology, 10(2), 455-460 I This work is licensed under a Creative Commons Attribution 4.0. License
