Next Article in Journal
Improving Rice Quality by Regulating the Heading Dates of Rice Varieties without Yield Penalties
Next Article in Special Issue
Aquatic Plants in Ponds at the Brdo Estate (Slovenia) Show Changes in 20 Years
Previous Article in Journal
Invasive Buttonweed Cotula coronopifolia (Asteraceae) Is Halotolerant and Has High Potential for Dispersal by Endozoochory
Previous Article in Special Issue
Interspecific Differences in Carbon and Nitrogen Metabolism and Leaf Epiphytic Bacteria among Three Submerged Macrophytes in Response to Elevated Ammonia Nitrogen Concentrations
 
 
Search for Articles:
Title / Keyword
Author / Affiliation / Email
Journal
Article Type
 
 
Advanced Search
 
Section
Special Issue
Volume
Issue
Number
Page
 
Journals
Plants
Volume 13
Issue 16
10.3390/plants13162220
plants-logo
Submit to this Journal Review for this Journal Propose a Special Issue
► Article Menu

Article Menu

share Share announcement Help format_quote Cite question_answer Discuss in SciProfiles thumb_up
...
Endorse textsms
...
Comment
first_page
settings
Order Article Reprints
Font Type:
Arial Georgia Verdana
Font Size:
Aa Aa Aa
Line Spacing:
Column Width:
Background:
Article

The Genetic Diversity of the Macrophyte Ceratophyllum demersum in Backwaters Reflects Differences in the Hydrological Connectivity and Water Flow Rate of Habitats

by
Attila I. Engloner
1,2,*,
Kitti Németh
1,2 and
Judit Bereczki
3
1
HUN-REN Centre for Ecological Research, Karolina út 29, H-1113 Budapest, Hungary
2
National Laboratory for Water Science and Water Security, HUN-REN Centre for Ecological Research, Karolina út 29, H-1113 Budapest, Hungary
3
Molecular Taxonomy Laboratory, Hungarian National Museum Public Collection Centre, Hungarian Natural History Museum, H-1083 Budapest, Hungary
*
Author to whom correspondence should be addressed.
Plants 2024, 13(16), 2220; https://doi.org/10.3390/plants13162220
Submission received: 3 July 2024 / Revised: 30 July 2024 / Accepted: 7 August 2024 / Published: 10 August 2024
(This article belongs to the Special Issue Physiology and Ecology of Aquatic Plants)
Browse Figures
Versions Notes

Abstract

:
Macrophytes often live in fluvial backwaters that have a variety of hydrological connections to a main river. Since the ability of these plants to adapt to changing environments may depend on the genetic diversity of the populations, it is important to know whether it can be influenced by habitat characteristics. We examined the microsatellite polymorphism of the submerged macrophyte Ceratophyllum demersum from various backwaters and showed that the genetic diversity of this plant clearly reflects habitat hydrological differences. The greatest genetic variability was found in a canal system where constant water flow maintained a direct connection between the habitats and the river. In contrast, an isolated backwater on the protected side of the river had the lowest plant genetic diversity. Oxbows permanently connected to the branch system with static or flowing water, and former river branches temporarily connected to the main bed contained populations with moderately high or low genetic variability. The results demonstrate that habitat fragmentation can be a result not only of the loss of direct water contact, but also of the lack of flowing water. Adverse hydrological changes can reduce the genetic diversity of populations and thus the ability of this macrophyte to adapt to changing environments.

1. Introduction

In fluvial ecosystems, backwaters can provide various habitats for aquatic organisms. Differences in water flow and connection types to the main river bed and other water bodies result in highly different hydrological conditions and can affect biodiversity in several ways [1,2,3]. Community and population diversity at the taxonomic, functional, and genetic levels within and between habitats may depend on the type of hydrological connections. The latter can range from complete, permanent connection through varied temporal and spatial separation to complete, permanent isolation [2]. Loss of connectivity leads to hydrological fragmentation, greatly reducing freshwater biodiversity and increasing the risk of extinction [4]. The severe consequences of habitat fragmentation on genetic diversity threaten a variety of freshwater organisms around the world [5]. Decreased gene flow and increased vulnerability to genetic drift, inbreeding and selection can both be a consequence of habitat fragmentation [6,7].
Aquatic macrophytes are completely dependent on the water supply of the habitat, which determines the conditions for their life and their colonization [8,9]. Since these plants have both sexual and asexual reproduction, colonization can occur through seeds and vegetative shoot fragments spread by animals, wind and water [10]. Both sexual reproduction and gene flow from distant areas increase the genetic diversity, and thus the potential adaptability of these plants to their environment [11,12]. Although the animals and wind may ensure the dispersal of macrophytes between isolated water bodies, hydrochory (that is, spread by water flow) cannot occur between backwaters without hydrological connections [13,14,15]. Therefore, when hydrochory is exclusive or dominant for a plant species, not only the amount of water in the given habitat, but also the degree of connectivity between different habitats, can be of great importance.
River systems provide a special environment for aquatic plants, enabling long-distance dispersal. Gene flow in linear, unidirectional river channels is easily understood and plant genetic structure in these habitats is well known, as genetic diversity increases downstream, suggesting that flow affects patterns of intrapopulation genetic diversity [16]. However, population genetic diversity in the water bodies of fluvial systems with various hydrological connections and water flow has been little investigated.
C. demersum is a cosmopolitan submerged macrophyte known for its low sexual reproduction and dispersal by shoot fragments carried by water flow [17,18,19,20,21,22]. Because microsatellites (i.e., short tandem repeats) are particularly informative and powerful markers for studying the genetic diversity and demographic processes of plants, Engloner et al. [23] developed microsatellite primers for this species and investigated its genetic diversity in lotic and lentic habitats. Compared to the backwaters, the authors showed greater population genetic variability in the main channel and tributaries of the river, where the flowing water provides a permanent longitudinal connection with distant habitats. Although microsatellite polymorphism in the backwaters proved to be diverse, no detailed analysis of the genetic variability of the populations related to hydrological differences has been made for these habitats. Given that aquatic macrophytes mostly live in still or slow-flowing waters [17], a thorough study of plant stands in different fluvial backwaters is essential to understand the effects of habitat hydrology on population genetic diversity, which may affect the ability of macrophytes to adapt to changing environments. The adaptability is particularly important in the backwater systems of rivers, where global climate change can cause significant hydrological changes [24,25].
For the above reasons, the aim of the present study is to explore the microsatellite polymorphism of the populations of the hydrochore C. demersum in river backwaters with different hydrological connections to the main bed, and to reveal whether the type of connection can affect the genetic diversity of this species in backwater systems.

2. Materials and Methods

2.1. Study Sites and Sampling

Plant material was collected from six aquatic habitats in Hungary, Central Europe (Figure 1). (i) Tisza Reservoir (T), also known as Lake Tisza, is an area of 127 km2 flooded by the dammed waters of Tisza River (47°40′12.00″ N, 20°45′30.18″ E). In this reservoir, a network of canals with constant water flow maintains the connection with the river. (ii) Schisler (S) and (iii) Zátonyi (Z) oxbows lie on the Szigetköz water plain, where many branches, islands and backwaters are spread between the main Danube channel and the Moson-arm (47°57′10.00″ N, 17°21′33.90″ E and 47°54′14.80″ N, 17°23′17.00″ E, respectively). Schisler has a direct, close connection with the Danube, which is 1.5 km away. The flow of water is intermittent but frequent. Zátonyi is part of the extensive branch system of the Szigetköz, far from the main river channel, with stagnant water. (iv) Decsi (D) and (v) Mocskos (M) oxbows are former Danube side branches lying on the floodplain of the Gemenc and Béda-Karapancsa Landscape Protection Areas (46°16′53.90″ N, 18°51′48.50″ E and 45°58′12.90″ N, 18°46′23.20″ E, respectively). Both can be temporarily connected to the Danube during the river’s floods, but with different frequencies. In the last fifty years, such an event has occurred only on a third of the days at Mocskos, and only on a sixth at Decsi [26]. (vi) Riha (R) is an isolated backwater on the protected side of the left bank of the Danube near Mohács (river km 1447), supported only by inland inundation (46°0′46.50″ N, 18°45′54.20″ E). The main hydrological differences in the six habitats are briefly summarized in Table 1.
In order to avoid sampling from the same plant (i.e., collecting multiple leaves of the same individual), a distance of at least 30 m was kept between two samples. The amount of plant cover at the habitats T, S, Z, D, M and R allowed for the collection of 20, 16, 8, 13, 10, and 27 plant samples for genetic investigations. Plant material was stored at 4 °C during transport to the laboratory, and then at −80 °C until DNA isolation.

2.2. Laboratory Work

DNA was extracted by homogenizing 200 mg frozen plant material in 800 μL CTAB isolation buffer (2%), following the protocol described in [27]. To study the microsatellite polymorphism, ten primer pairs were used according to Engloner et al. [23]. One out of ten loci (namely HME24) was monomorphic in all samples and was therefore omitted from the analyses. During amplification, we used the fluorescent dye-labeled primers described by the authors mentioned above. The amplification procedure from 5 μL of DNA extracts was carried out in 15 μL final reaction volumes containing 10× PCR buffer, 3 mM MgCl2, 0.2 mM dNTPs, 0.05 units/μL of Taq DNA polymerase (Taq DNA Polymerase, recombinant, Fermentas), and 0.5 μM of each primer. The cycling conditions were used as provided by Engloner et al. [23]. After amplification, the PCR products were multiplexed in a single reaction and fragment analysis was carried out on an ABI 3130 Genetic Analyser (Hitachi, Tokyo, Japan). Allele sizes were estimated using Peak Scanner software v1.0 (Thermo Fisher Scientific, Waltham, MA, USA).

2.3. Statistical Analyses

Micro-Checker 2.2.3 [28] was used for calculating the null allele frequency by Monte Carlo simulation of the expected homozygote frequencies and heterozygote allele size differences. The Micro-Checker analysis did not detect systematic evidence for null alleles at any of the studied microsatellite loci; thus, the whole data set was used for further analyses. The parameters of polymorphism were determined using GenAlEx v. 6.5 [29,30] and Fstat v. 2.9.4 [31]. Among the variability parameters, the number of effective alleles and allelic richness make it possible to compare the genetic variability of populations even with different sample sizes [32,33].
Genetic variation was also characterized by the total allele pool of the backwaters sorted to common (detected in all backwaters) and specific (detected in the given backwater only) alleles.
To reveal the genetic differentiation among plant samples from the six selected habitats, the microsatellite allele frequency data were evaluated by standardized principal component analysis (PCA) using the SYN-TAX 2000 computer program package [34]. This multivariate statistical method is useful for revealing and visualizing differences between objects (in this case plant samples) and groups of objects (samples of the populations) based on all variables (allele frequencies). The distances between objects and object groups displayed as a result of PCA are proportional to the genetic variability between them.
The genetic structure of the populations was analyzed using the Bayesian clustering method [35]. The most probable number of genetically differentiated groups (K) in the populations was estimated and the individuals were assigned to these groups. Structure 2.3.4 was run to carry out these analyses using default settings, with an initial burn in of 100,000 steps and running length of 500,000 steps. In the evaluation of the results, ΔK was computed, which indicates the change in log probability between successive K values [36]. The package ‘pophelper’ in R [37] was applied to compute the ΔK values, average the ten runs of the most probable K value given by Structure, and correct for label switching.

3. Results

The level of genetic variability proved to be highly different among the C. demersum samples (Table 2). The Tisza Reservoir showed the greatest diversity in terms of almost all parameters (except MG), while the Riha generally had the smallest. The average number of alleles per locus was 2.630; the highest was in the Tisza Reservoir (4.444), and the lowest in the Riha backwater (1.667). The variability parameters corrected for sample size, i.e., the number of effective alleles and the allelic richness, in total were 1.990 and 3.611, respectively. Based on these two parameters and Shannon’s information index, the genetic variability decreases in the following order: Tisza Reservoir > Mocskos, Schisler > Zátonyi > Decsi > Riha. The positions of Mocskos and Schisler are swapped in the row when they are ranked by the number of effective alleles or the allelic richness and Shannon’s information index. A total of 40 different multilocus genotypes were detected: the most in Schisler and the least in Decsi oxbow. Overall, more than 80% of the loci proved to be polymorphic, and this value reached 100% in the Tisza Reservoir and the Mocskos backwater.
The allele pool of C. demersum amounted to 54 at the nine loci analyzed. The total number of alleles differed largely among the samples (Figure 2). The highest number was observed in Tisza Reservoir (N = 40), the lowest in Decsi backwater (N = 15), and between them it decreased in the following order: Mocskos > Schisler > Zátonyi > Riha. The distribution of alleles between the common and specific classes was also different in the samples. The highest portion of the backwater-specific alleles (N = 16) was observed in Tisza Reservoir, while Riha did not harbor private alleles at all.
The ordination of microsatellite data resulted in well-separated groups of samples taken from the six habitats, and only the samples of Riha and Mocskos backwaters overlapped to some extent (Figure 3). As the areas of the polygons enclosing objects in the scattergram are proportional to the variability between the objects (i.e., the larger the area the higher the variability), the result shows the highest genetic variability of C. demersum in Tisza Reservoir, followed by the Mocskos and Schisler oxbows, and the lowest in the other three habitats.
The most probable number of genetically differentiated groups (K) proved to be four in the Structure analysis (Figure 4 and Figure 5). Tisza Reservoir, Decsi and Riha backwaters are clearly separated from each other and from the genetic unit formed by Schisler and Zátonyi, which are not separated by the program at K = 4. Meanwhile, the software defines the Mocskos oxbow as most likely a mixture of the two former backwaters and the Riha.

4. Discussion

Since both sexual and asexual reproduction and dispersal by seeds and vegetative shoot fragments can occur in plants, the ratio of these processes, and the predominance of one or the other, highly determines their genetic diversity. In populations of aquatic macrophytes, genetic diversity may be particularly low due to a higher ratio of clonal reproduction and the long-term persistence of the clones [10,38]. Somatic mutations can also increase genetic diversity in clonally spread populations, which is enhanced by rapid clonal growth and a large number of vegetative propagules [38,39,40,41]; however, no somatic mutation associated with C. demersum has been reported.
Gene flow from a distant population can also be limited as aquatic habitats are more geographically isolated than terrestrial ones [38]. The wide distribution ranges of many aquatic plants are often considered evidence of high bird-mediated dispersal [10]. Rivers, however, can also provide long-distance dispersal for hydrochore species, resulting in greater genetic variability downstream than upstream [42], and in a main channel and its tributaries than in backwaters [23]. The latter habitats may have various—absent, permanent or temporal—hydrological connections with the main bed and tributaries, providing different opportunities for spreading with water flow. The importance of temporal connection caused by floods in the establishment of coastal populations has already been proven in the marine zones behind the dune systems [14], but the effects of habitat hydrology on the spread of hydrochore macrophytes in river backwaters have not been investigated so far.
This study provides the first results on the genetic diversity of macrophyte populations from backwaters with different hydrological characteristics. Based on the identified multilocus genotypes, these populations were well-separated, and only the Mocskos oxbow appeared to be a home to the genetic mixture of the individual samples of two upstream backwaters (Schisler and Zátonyi) and the closest water body (Riha). Downstream gene flow through the main river channel is easy to understand [42], but the genetic mixing between the Mocskos and Riha backwaters, separated by the embankment, may have two explanations. These two water bodies are very close to each other and were located on the same floodplain before the river regulation. Therefore, the partially shared genetic makeup is either the remnants of the former hydrological connection or a sign of water-independent spread. If the latter occurs at all, it should be to a low degree, given that the distribution of this species relies on vegetative fragments rather than pollen or seeds [20,22].
The variability revealed in the microsatellite polymorphism shows that the genetic diversity of the C. demersum populations clearly reflects the habitat hydrological differences. The greatest genetic variability was found in the canal system (Tisza Reservoir), where the constant water flow maintains a direct connection between the habitats and the river. In contrast, macrophytes from the isolated backwater, located on the protected side of the river and supported only by inland water (Riha), showed the lowest genetic diversity. The genetic variability of the other investigated backwater populations fell between this maximum and minimum, depending on the strength of hydrological connectivity and the rate of water flow. In the backwater permanently connected to the branch system, but with static water (Zátonyi), the genetic diversity of the population is moderately low, just as in the former river branch temporarily connected to the main bed during rare flood events (Decsi). Greater genetic variability can be observed in an earlier side branch where flooding is more frequent (Mocskos), and in a backwater with a permanent, close connection to the river, where water can often flow (Schisler).
This clear correlation between habitat hydrology and the genetic variability of a macrophyte with low sexual reproduction and mainly hydrochore spread may mean that adverse hydrological changes may reduce the genetic diversity of these populations. Harmful changes in habitat hydrology can be the result of both global climate change [24,25] and any other human intervention [12]. Habitat fragmentation, in the sense that it impedes gene flow from distant areas [6], can be a result of these plants not only through the loss of direct water contact, but also through the lack of flowing water. In fact, as our results demonstrated, habitats that are periodically totally isolated but frequently flooded by a river may allow for greater macrophyte genetic diversity than those that are connected to distant water bodies by permanent but standing water. As population genetic diversity can greatly affect the ability of plants to adapt to changing environments, it is of great importance to know how this genetic diversity depends on different habitat characteristics.
The correlation between habitat hydrology, genetic variability, and the adaptability of plants to changing environments also draws attention to the importance of conservation implications and the need for possible management strategies. Genetic diversity and adaptive potential (i.e., genetic recovery) can be increased through habitat reconnection or human-assisted translocations [5]. However, the resilience of the reintroduced seeds and plant material may be problematic due to future environmental stress, so the design of mixed propagation lines may become necessary [43]. In fluvial systems, the increase in the length and number of free-flowing river sections can be a solution to restoring habitats and protecting biodiversity [44].

5. Conclusions

In fluvial systems, macrophytes face the hydrological variability of their habitat, which describes differences in water flow and connection types to the main river bed and other water bodies. Examination of the microsatellite polymorphism of the hydrochore macrophyte C. demersum from different backwaters showed that the genetic diversity of this plant clearly reflects habitat hydrological differences. Population genetic variability is greatest if constant water flow maintains a direct connection between the habitats and the river, while plant genetic diversity is lowest in a completely isolated backwater. Furthermore, oxbows that are periodically totally isolated but frequently flooded by a river may allow for greater macrophyte genetic diversity than those that are connected to distant water bodies by permanent but standing water. Habitat fragmentation can therefore be the result not only of the loss of direct water contact, but also of the lack of flowing water. Since the ability of plants to adapt to a changing environment depends on the genetic diversity of their populations, which is, however, determined by the degree of gene flow from distant areas, the fragmentation of a habitat increases the vulnerability of these populations. Mitigating the effects of adverse hydrological changes resulting from global climate change and any other human activities may require conservation interventions and management strategies. Of course, the ratio of sexual and asexual reproduction and the dispersal of seeds and vegetative shoots are different in macrophytes; therefore, the effects of hydrological connectivity and water flow on population genetic variability should be investigated in additional species.

Author Contributions

Conceptualization, A.I.E.; methodology, A.I.E. and J.B.; formal analysis, A.I.E. and J.B.; investigation, A.I.E., K.N. and J.B.; resources, A.I.E.; data curation, A.I.E. and J.B.; writing—original draft preparation, A.I.E., K.N. and J.B.; writing—review and editing, A.I.E. and J.B.; visualization, A.I.E., K.N. and J.B.; funding acquisition, A.I.E. All authors have read and agreed to the published version of the manuscript.

Funding

The research presented in the article was carried out within the framework of the Széchenyi Plan Plus program with the support of the RRF 2.3.1 21 2022 00008 project.

Data Availability Statement

Data are contained within the article.

Acknowledgments

The authors thank Eduárd Csépes (Central Tisza Region Water Directorate) for his help in sampling in the Tisza Reservoir.

Conflicts of Interest

The authors declare no conflict of interest.

References

  1. Bayley, P.B. Understanding large river-floodplain ecosystems. BioScience 1995, 45, 153–158. [Google Scholar] [CrossRef]
  2. Amoros, C.; Bornette, G. Connectivity and biocomplexity in waterbodies of riverine floodplains. Freshw. Biol. 2002, 47, 761–776. [Google Scholar] [CrossRef]
  3. Guan, Q.; Wu, H.; Xu, L.; Kang, Y.; Lu, K.; Liu, D.; Han, D.; Xue, Z.; Yuan, Y.; Wang, W.; et al. Hydrological connectivity shapes multiple diversity facets of snail (Mollusca: Gastropoda) assemblages in freshwater floodplain wetlands. Ecol. Indic. 2023, 153, 110467. [Google Scholar] [CrossRef]
  4. Brauer, C.J.; Beheregaray, L.B. Recent and rapid anthropogenic habitat fragmentation increases extinction risk for freshwater biodiversity. Evol. Appl. 2020, 13, 2857–2869. [Google Scholar] [CrossRef]
  5. Pavlova, A.; Beheregaray, L.B.; Coleman, R.; Gilligan, D.; Harrisson, K.A.; Ingram, B.A.; Kearns, J.; Lamb, A.M.; Lintermans, M.; Lyon, J.; et al. Severe consequences of habitat fragmentation on genetic diversity of an endangered Australian freshwater fish: A call for assisted gene flow. Evol. Appl. 2017, 10, 531–550. [Google Scholar] [CrossRef]
  6. Fan, X.R.; Njeri, H.K.; Li, W.; Chen, Y.Y. Abundant historical gene flow within and among river systems for populations of Ottelia acuminata var. jingxiensis, an endangered macrophyte from southwest China. Aquat. Bot. 2019, 157, 1–9. [Google Scholar] [CrossRef]
  7. Wu, Z.; Xu, X.; Zhang, J.; Wiegleb, G.; Hou, H. Influence of environmental factors on the genetic variation of the aquatic macrophyte Ranunculus subrigidus on the Qinghai-Tibetan Plateau. BMC Evol. Biol. 2019, 19, 228. [Google Scholar] [CrossRef]
  8. Reitsema, R.E.; Wolters, J.-W.; Preiner, S.; Meire, P.; Hein, T.; De Boeck, G.; Blust, R.; Schoelynck, J. Response of submerged macrophyte growth, morphology, chlorophyll content and nutrient stoichiometry to increased flow velocity and elevated CO2 and dissolved organic carbon concentrations. Front. Environ. Sci. 2020, 11, 527801. [Google Scholar] [CrossRef]
  9. Goldenberg-Vilar, A.; Delgado, C.; Penas, F.J.; Barquín, J. The effect of altered flow regimes on aquatic primary producer communities: Diatoms and macrophytes. Ecohydrology 2022, 15, e2353. [Google Scholar] [CrossRef]
  10. Santamaría, L. Why are most aquatic plants widely distributed? Dispersal, clonal growth and small-scale heterogeneity in a stressful environment. Acta Oecol. 2002, 23, 137–154. [Google Scholar] [CrossRef]
  11. Cao, Q.; Hu, F.; Liu, N. Local-scale patterns of genetic variation in coexisting floating-leaved Nymphoides peltata and submerged Myriophyllum spicatum in Donghu Lake. J. Oceanol. Limnol. 2020, 38, 1825–1834. [Google Scholar] [CrossRef]
  12. Cao, Q.; Liu, B.; Hu, F. Effects of hydrological connection and human disturbance on genetic variation of submerged Vallisneria natans populations in four lakes in China. J. Oceanol. Limnol. 2021, 39, 1403–1416. [Google Scholar] [CrossRef]
  13. Chen, Y.; Li, X.; Yin, L.; Cheng, Y.; Li, W. Genetic diversity and migration patterns of the aquatic macrophyte Potamogeton malaianus in a potamolacustrine system. Freshw. Biol. 2009, 54, 1178–1188. [Google Scholar] [CrossRef]
  14. Triest, L.; Tran Thi, V.; Le Thi, D.; Sierens, T.; Van Geert, A. Genetic differentiation of submerged plant populations and taxa between habitats. Hydrobiologia 2010, 656, 15–27. [Google Scholar] [CrossRef]
  15. Jones, P.E.; Consuegra, S.; Börger, L.; Jones, J.; Garcia de Leaniz, C. Impacts of artificial barriers on the connectivity and dispersal of vascular macrophytes in rivers: A critical review. Freshw. Biol. 2020, 65, 1165–1180. [Google Scholar] [CrossRef]
  16. Pollux, B.J.A.; Luteijn, A.; Van Groenendael, J.M.; Ouborg, N.J. Gene flow and genetic structure of the aquatic macrophyte Sparganium emersum in a linear unidirectional river. Freshw. Biol. 2009, 54, 64–76. [Google Scholar] [CrossRef]
  17. Arber, A. Water Plants; Cambridge University Press: London, UK, 1920. [Google Scholar]
  18. Les, D.H. The phytogeography of Ceratophyllum demersum and C. echinatum (Ceratophyllaceae) in glaciated North America. Can. J. Bot. 1986, 64, 498–509. [Google Scholar] [CrossRef]
  19. Les, D.H. Genetic diversity in the monoecious hydrophile Ceratophyllum (Ceratophyllaceae). Am. J. Bot. 1991, 78, 1070–1082. [Google Scholar] [CrossRef]
  20. Wade, P.M. The influence of vegetation pre-dredging on the post-dredging community. J. Aquat. Plant Manag. 1993, 31, 141–144. [Google Scholar]
  21. Fukuhara, H.; Tanaka, T.; Izumi, M. Growth and turion formation of Ceratophyllum demersum in a shallow lake in Japan. Jpn. J. Limnol. 1997, 58, 335–347. [Google Scholar] [CrossRef]
  22. Capers, R.S. Macrophyte colonization in a freshwater tidal wetland (Lyme, CT, USA). Aquat. Bot. 2003, 77, 325–338. [Google Scholar] [CrossRef]
  23. Engloner, A.I.; Németh, K.; Kós, P.B.; Meglécz, E.; Bereczki, J. Genetic diversity of the submerged macrophyte Ceratophyllum demersum depends on habitat hydrology and habitat fragmentation. Front. Plant Sci. 2023, 14, 1277916. [Google Scholar] [CrossRef] [PubMed]
  24. O’Briain, R. Climate change and European rivers: An eco-hydromorphological perspective. Ecohydrology 2019, 12, e2099. [Google Scholar] [CrossRef]
  25. Rivaes, R.P.; Feio, M.J.; Almeida, S.F.P.; Calapez, A.R.; Sales, M.; Gebler, D.; Lozanovska, I.; Aguiar, F.C. River ecosystem endangerment from climate change-driven regulated flow regimes. Sci. Total Environ. 2022, 818, 151857. [Google Scholar] [CrossRef] [PubMed]
  26. Hungarian Hydrological Forecasting Service. Available online: https://www.hydroinfo.hu/en/index.html (accessed on 2 July 2024).
  27. Bousquet, J.; Simon, L.; Lalonde, M. DNA amplification from vegetative and sexual tissues of trees using polymerase chain reaction. Can. J. For. Res. 1990, 20, 254–257. [Google Scholar] [CrossRef]
  28. Van Oosterhout, C.; Hutchinson, W.F.; Wills, D.P.M.; Shipley, P. MICRO-CHECKER: Software for identifying and correcting genotyping errors in microsatellite data. Mol. Ecol. Notes 2004, 4, 535–538. [Google Scholar] [CrossRef]
  29. Peakall, R.; Smouse, P.E. GENALEX 6: Genetic analysis in Excel. Population genetic software for teaching and research. Mol. Ecol. Notes 2006, 6, 288–295. [Google Scholar] [CrossRef]
  30. Peakall, R.; Smouse, P.E. GenAlEx 6.5: Genetic analysis in Excel. Population genetic software for teaching and research–an update. Bioinformatics 2012, 28, 2537–2539. [Google Scholar] [CrossRef]
  31. Goudet, J. Fstat (ver. 2.9.4), a Program to Estimate and Test Population Genetics Parameters. Available online: http://www2.unil.ch/popgen/softwares/fstat.htm (accessed on 11 August 2023).
  32. Leberg, P.L. Estimating allelic richness: Effects of sample size and bottlenecks. Mol. Ecol. 2002, 11, 2445–2449. [Google Scholar] [CrossRef]
  33. Weir, B.S. Genetic Data Analysis. Methods for Discrete Population Genetic Data; Sinauer Associates Inc.: Sunderland, MA, USA, 1990; pp. 124–125. [Google Scholar]
  34. Podani, J. SYN-TAX Computer Programs for Data Analysis in Ecology and Systematics; User’s Manual; Scientia: Budapest, Hungary, 2001. [Google Scholar]
  35. Pritchard, J.K.; Stephens, M.; Donnelly, P. Inference of population structure using multilocus genotype data. Genetics 2000, 155, 945–959. [Google Scholar] [CrossRef]
  36. Evanno, G.; Regnaut, S.; Goudet, J. Detecting the number of clusters of individuals using the software STRUCTURE: A simulation study. Mol. Ecol. 2005, 14, 2611–2620. [Google Scholar] [CrossRef] [PubMed]
  37. Francis, R.M. POPHELPER: An R package and web app to analyse and visualize population structure. Mol. Ecol. Resour. 2017, 17, 27–32. [Google Scholar] [CrossRef] [PubMed]
  38. Kong, F.; Wu, Z.; Wang, H.; Chen, J.; Xu, X. Population genetic structure of the whorl-leaf watermilfoil Myriophyllum verticillatum shaped by topography and geographic distance. Hydrobiologia 2019, 838, 55–64. [Google Scholar] [CrossRef]
  39. de Witte, L.C.; Stöcklin, J. Longevity of clonal plants: Why it matters and how to measure it. Ann. Bot. 2010, 106, 859–870. [Google Scholar] [CrossRef] [PubMed]
  40. Eckert, G.C.; Dorken, M.E.; Barrett, S.C.H. Ecological and evolutionary consequences of sexual and clonal reproduction in aquatic plants. Aquat. Bot. 2016, 135, 46–61. [Google Scholar] [CrossRef]
  41. Zhu, J.; Xu, X.; Tao, Q.; Yi, P.; Yu, D.; Xu, X. High invasion potential of Hydrilla verticillata in the Americas predicted using ecological niche modeling combined with genetic data. Ecol. Evol. 2017, 7, 4982–4990. [Google Scholar] [CrossRef] [PubMed]
  42. Gornall, R.J.; Hollingsworth, P.M.; Preston, C.D. Evidence for spatial structure and directional gene flow in a population of an aquatic plant, Potamogeton coloratus. Heredity 1998, 80, 414–421. [Google Scholar] [CrossRef]
  43. Coppi, A.; Lastrucci, L.; Carta, A.; Foggi, B. Analysis of genetic structure of Ranunculus baudotii in a Mediterranean wetland. Implications for selection of seeds and seedlings for conservation. Aquat. Bot. 2015, 126, 25–31. [Google Scholar] [CrossRef]
  44. Stoffers, T.; Altermatt, F.; Baldan, D.; Bilous, O.; Borgwardt, F.; Buijse, A.D.; Bondar-Kunze, E.; Cid, N.; Erős, T.; Ferreira, M.T.; et al. Reviving Europe’s rivers: Seven challenges in the implementation of the Nature Restoration Law to restore free-flowing rivers. WIREs Water 2024, 11, e1717. [Google Scholar] [CrossRef]
Plants 13 02220 g001
Figure 1. Sampling locations. T—Tisza Reservoir; S—Schisler; Z—Zátonyi; D—Decsi; M—Mocskos and R—Riha backwaters.
Figure 1. Sampling locations. T—Tisza Reservoir; S—Schisler; Z—Zátonyi; D—Decsi; M—Mocskos and R—Riha backwaters.
Plants 13 02220 g001
Plants 13 02220 g002
Figure 2. Distribution of alleles among the different classes in the backwaters. Common: detected in all backwaters; specific: detected in the given backwater only. T—Tisza Reservoir; S—Schisler; Z—Zátonyi; D—Decsi; M—Mocskos and R—Riha backwaters.
Figure 2. Distribution of alleles among the different classes in the backwaters. Common: detected in all backwaters; specific: detected in the given backwater only. T—Tisza Reservoir; S—Schisler; Z—Zátonyi; D—Decsi; M—Mocskos and R—Riha backwaters.
Plants 13 02220 g002
Plants 13 02220 g003
Figure 3. PCA ordination of C. demersum samples based on microsatellite allele frequency data. Convex polygons enclose plant samples collected from the same habitats. T—Tisza Reservoir; S—Schisler; Z—Zátonyi; D—Decsi; M—Mocskos and R—Riha backwaters.
Figure 3. PCA ordination of C. demersum samples based on microsatellite allele frequency data. Convex polygons enclose plant samples collected from the same habitats. T—Tisza Reservoir; S—Schisler; Z—Zátonyi; D—Decsi; M—Mocskos and R—Riha backwaters.
Plants 13 02220 g003
Plants 13 02220 g004
Figure 4. Bayesian assignment of individuals from 6 populations to genetic clusters inferred from the analysis of 9 microsatellite loci for K = 4. T—Tisza Reservoir; S—Schisler; Z—Zátonyi; D—Decsi; M—Mocskos and R—Riha backwaters. The plot represents each individual as a thin vertical bar. The proportion of each color in each column indicates the proportion of an individual’s genome being classified in any of the 4 clusters.
Figure 4. Bayesian assignment of individuals from 6 populations to genetic clusters inferred from the analysis of 9 microsatellite loci for K = 4. T—Tisza Reservoir; S—Schisler; Z—Zátonyi; D—Decsi; M—Mocskos and R—Riha backwaters. The plot represents each individual as a thin vertical bar. The proportion of each color in each column indicates the proportion of an individual’s genome being classified in any of the 4 clusters.
Plants 13 02220 g004
Plants 13 02220 g005
Figure 5. An Evanno method output plot. ΔK obtained by the package ‘pophelper’ in which R indicates the change in log probability between successive K values.
Figure 5. An Evanno method output plot. ΔK obtained by the package ‘pophelper’ in which R indicates the change in log probability between successive K values.
Plants 13 02220 g005
Table 1. A brief summary of the main hydrological differences in the six investigated habitats.
Table 1. A brief summary of the main hydrological differences in the six investigated habitats.
Connection to the RiverbedFlow of Water
Tisza-Reservoir (T)permanent, closepermanent
Schisler (S)permanent, closetemporary
Zátonyi (Z)permanent, distantabsent
Decsi (D)temporary, raretemporary
Mocskos (M)temporary, moderately raretemporary
Riha (R)absentabsent
Table 2. The parameters of variability based on 9 microsatellite loci.
Table 2. The parameters of variability based on 9 microsatellite loci.
NNaNeARIMG%P
Tisza-Reservoir (T)19.7784.4442.6053.7261.02310100.00
Schisler (S)15.7782.5562.3112.5290.7811377.78
Zátonyi (Z)8.0002.4441.8732.4440.630377.78
Decsi (D)13.0001.6671.6651.6670.462266.67
Mocskos (M)10.0002.8892.1252.8170.8048100.00
Riha (R)27.0001.7781.3591.5050.285566.67
Total15.5932.6301.9903.6110.6644081.48
N—sample size; Na—average number of alleles per locus; Ne—the number of effective alleles; AR—allelic richness (N = 8); I—Shannon’s information index; MG—the number of multilocus genotypes; P%—percentage of polymorphic loci on the basis of the 95% criterion.
Disclaimer/Publisher’s Note: The statements, opinions and data contained in all publications are solely those of the individual author(s) and contributor(s) and not of MDPI and/or the editor(s). MDPI and/or the editor(s) disclaim responsibility for any injury to people or property resulting from any ideas, methods, instructions or products referred to in the content.

Share and Cite

MDPI and ACS Style

Engloner, A.I.; Németh, K.; Bereczki, J. The Genetic Diversity of the Macrophyte Ceratophyllum demersum in Backwaters Reflects Differences in the Hydrological Connectivity and Water Flow Rate of Habitats. Plants 2024, 13, 2220. https://doi.org/10.3390/plants13162220

AMA Style

Engloner AI, Németh K, Bereczki J. The Genetic Diversity of the Macrophyte Ceratophyllum demersum in Backwaters Reflects Differences in the Hydrological Connectivity and Water Flow Rate of Habitats. Plants. 2024; 13(16):2220. https://doi.org/10.3390/plants13162220

Chicago/Turabian Style

Engloner, Attila I., Kitti Németh, and Judit Bereczki. 2024. "The Genetic Diversity of the Macrophyte Ceratophyllum demersum in Backwaters Reflects Differences in the Hydrological Connectivity and Water Flow Rate of Habitats" Plants 13, no. 16: 2220. https://doi.org/10.3390/plants13162220

Note that from the first issue of 2016, this journal uses article numbers instead of page numbers. See further details here.

Article Metrics

Back to TopTop