Genetic diversity in three invasive clonal aquatic species in New Zealand
© Lambertini et al; licensee BioMed Central Ltd. 2010
Received: 3 March 2010
Accepted: 18 June 2010
Published: 18 June 2010
Elodea canadensis, Egeria densa and Lagarosiphon major are dioecious clonal species which are invasive in New Zealand and other regions. Unlike many other invasive species, the genetic variation in New Zealand is very limited. Clonal reproduction is often considered an evolutionary dead end, even though a certain amount of genetic divergence may arise due to somatic mutations. The successful growth and establishment of invasive clonal species may be explained not by adaptability but by pre-existing ecological traits that prove advantageous in the new environment. We studied the genetic diversity and population structure in the North Island of New Zealand using AFLPs and related the findings to the number of introductions and the evolution that has occurred in the introduced area.
Low levels of genetic diversity were found in all three species and appeared to be due to highly homogeneous founding gene pools. Elodea canadensis was introduced in 1868, and its populations showed more genetic structure than those of the more recently introduced of E. densa (1946) and L. major (1950). Elodea canadensis and L. major, however, had similar phylogeographic patterns, in spite of the difference in time since introduction.
The presence of a certain level of geographically correlated genetic structure in the absence of sexual reproduction, and in spite of random human dispersal of vegetative propagules, can be reasonably attributed to post-dispersal somatic mutations. Direct evidence of such evolutionary events is, however, still insufficient.
Invasive plants are of evolutionary interest because they are successful in areas where they have been introduced, sometimes in spite of limited genetic variation compared to their native range. One reason for this success may be multiple introductions, representing genetically distant genotypes. Further, an introduced species can overcome the negative effects of genetic bottlenecks and create genetic variation in the introduced range when genotypes from different geographical areas are brought together, giving rise to genetic combinations resulting in novel genotypes not present in the native range. In the case of Phalaris arundinacea L. in North America, the genetic variation is even comparable to that found in the native European range . Apparently, however, many plant species become successful invaders in spite of very limited or non-existing genetic variation. This is the case in perennial clonal species, which establish themselves and disperse by vegetative propagation. Examples are the tropical American aquatic species Alternanthera philoxeroides (C. Martius) Griseb.  and Eichornia crassipes (C. Martius) Solms-Laub.  in their introduced range in China.
Clonal growth is often considered an evolutionary dead end, as defined by Stebbins  for self-fertilized plants. Somatic mutations do occur, although not frequently, and their role in the evolution of clonal species has been extensively modelled .According to the somatic mutation theory of clonality of Klekowski [6, 7] plants accumulate mutations in meristematic cells with age. Such mutations reduce the likelihood of sexual reproduction and after a certain time, evolutionary changes depend exclusively on somatic mutations with advantageous phenotypes. It is assumed that sexual reproduction reduces genetic diversity by preventing somatic mutations from being transmitted to the offspring . In this respect the structure and organization of meristems (monopodial vs. sympodial branching) affects the somatic mutation load that can be transferred to gametes . The concept of population as a group of interbreeding individuals is not obviously applicable to clonal species. A "population" of a clonal species could be said to be represented by a group of stands of which each may consist of one or more genotypes (clones). In contrast to the situation in obligately outbreeding sexually reproducing organisms, monoclonal "populations" are common  and even in the case of clonal diversity, Hardy-Weinberg equilibrium cannot be expected to occur, as sexual reproduction may occur sporadically, if at all.
The North Island of New Zealand (NZ) is a suitable area for the study of genetic variation patterns of invasive species because, being an island, it is naturally delimited, and the site of many plant invasions that have been thoroughly monitored and documented. In addition, NZ has only recently been colonized by Europeans and therefore provides a unique opportunity to study recent invasion pathways and spread, as well as habitat adaptation. Elodea canadensis Michaux, Lagarosiphon major (Ridley) Moss and Egeria densa Planchon are invasive in NZ and in many other parts of the world. They are all dioecious Hydrocharitaceae and, like many submerged clonal macrophytes, rarely achieve sexual reproduction even in the native range . Elodea canadensis is native to North America and was introduced in NZ in 1868 . Egeria densa is native to South America (Brazil, Argentina and Paraguay) and was introduced in NZ in 1946 . Lagarosiphon major is native to South Africa and was first recorded in NZ in 1950 . Only female plants of E. canadensis  and L. major  and male plants of E. densa  have been found in NZ. One single record from 1988 (I.M. Johnstone, NZ Electricity Department, pers. comm.) also reported male plants of E. canadensis from the Waingaro River (Waikato Region, Central North Island) but this appears to be an isolated record, as male plants have not been featured in subsequent surveys of the aquatic vegetation throughout NZ. Even though both E. canadensis sexes might potentially co-exist in some waters, seeds have never been observed in any of the three species . This limits interbreeding opportunities and excludes the possibility of hybridization between the three not so distantly related species, as well as agamospermy. The similar histories, the shared geographical setting and the apparent absence of sexual reproduction make this system suitable for the study of differentiation in invasive clonal species. The distribution and history of spread of these species in the North Island, documented by historical floristic records of first introduction date, suggest one single introduction for both E. densa and L. major , but this has never been critically tested with molecular markers. The same is true also for E. canadensis [11, 13], but in this case the floristic records are less complete, and historical scenario for the history of the species in NZ is even more speculative. The possibility of multiple introductions of E. canadensis was pointed out by Thomson  who provided evidence for repeated introduction of live fresh-water fish to New Zealand from Tasmania, where E. canadensis was already established at the time. In this study we attempt to determine the number of introductions and evaluate the role of somatic mutations and dispersal as possible sources of the genetic variation patterns observed. We have used AFLPs (Amplified Fragment Length Polymorphism; ), because of the high number of DNA markers that this technique is able to detect. This aspect is important when identifying identical genotypes, and when assessing small genetic differences between clones. We employed some precautions to recognize and exclude possible AFLP artefactual polymorphic fragments.
A larger number of polymorphic fragments was present in E. canadensis and E. densa and the interpretation of their patterns was less straightforward than in L. major. In E. canadensis (Figure 9c) the populations of McLaren, Oraka, Rotorua, Awakaponga and Pongakawa showed more frequent exchanges between each other than with the more distant, upstream populations of Otamangakau and Taupo South, which, likewise, were genetically more similar to each other than to the other populations. McLaren and Awakaponga had the highest number of polymorphic fragments shared with the other populations and appear to be important nodes for the dispersal and/or recruitment of this species. McLaren was found to be an important dispersal node also for E. densa (Figure 9b), and Parkinsons Lake for E. densa populations located in the NW part of the island. The Ngakeketa population from Northland shared polymorphic fragments with the neighbouring population of Swan and with Parkinsons Lake, but also with McLaren-connected populations, revealing long-distance dispersal. Long-distance dispersal appeared, however, less frequent than dispersal between neighbouring populations.
The DNA quality, the reproducibility of AFLP chromatograms, the different patterns observed in E. canadensis compared to E. densa and L. major and the similar geographical separation of Otamangakau and Taupo South populations both in E. canadensis and in L. major, indicate that AFLPs are appropriate for the study of genetic variation in these clonal species. If the observed genetic patterns were due to artefacts of the AFLP technique, similar results would have been expected in the three species, considering the similarly low levels of genetic variation.
Number of introductions
Low levels of genetic diversity were found in all three species, which suggest one introduction or multiple introductions of similar genotypes for each of the three species in the northern part of the North Island, NZ. High levels of genetic diversity in invasive species may be the result of multiple introductions [1, 17]. However it is not possible to exclude multiple introductions even in cases with low genetic diversity, as the introduced genotypes might be highly similar to begin with. The genetic variation pattern in the native range is an important reference point of the natural variability within an invasive species and can support the hypotheses of single vs. multiple introductions. The situation in invasive species can, however, be more complicated than this, as they may be derived from areas in the introduced rather than the native range, which can be expected to give rise to different patterns. Such a high level of genetic similarity as that observed in this study was unexpected and is an important finding for further genetic research in these and other invasive species. A geographically wider set of samples, including many native and introduced populations, would need to be analysed to conclusively address the number of introductions in NZ. In the case of L. major, genetic variation within and between populations in the native range in South Africa was studied by Triest  using isozymes. Most of the populations were unisexual and monoclonal. Low variation levels were recorded also between populations, indicating predominant vegetative propagation. Evidence of sexual reproduction was provided by the presence of one heterozygotic clone in an otherwise homozygotic, bisexual population. The polymorphism between this clone and the most spread one was 9.5%, which, interestingly, is comparable with the level of polymorphism found in our study (9.8%). However, in the NZ populations this level of diversity was based on the whole sample set. The two most different genotypes had a polymorphism of 5.6%, and it decreased to 3.5% and 2.1% if differences between these clones and the most widespread one were considered. Our study shows lower levels of polymorphism than between the two different genotypes in the native range; however some more samples from South Africa should be analysed to estimate the variability in the native range. In addition, the different markers applied in the two studies (isozyme vs. AFLPs) are not totally comparable because the amount and the parts of the genome analysed in the two studies are very different and AFLPs are designed to detect higher levels of intraspecific polymorphism than isozymes.
Genetic diversity was studied in introduced populations of E. densa in Oregon (USA) and Chile using RAPDs by Carter and Sytsma . Very little variation was found in these populations, and surprisingly the same genotypes were found in Oregon and Chile, suggesting low genetic diversity in the native source populations and/or similar introduction histories in the new ranges. Clones were genetically very similar to each other and the very short genetic distances between strains, as indicated by the UPGMA tree suggest a situation siMilar to that in the present study even though the molecular techniques used are different. The study of Carter and Systma  shows that multiple introductions of E. densa cannot be ruled out in the North Island, NZ. A stepping-stone model of colonization could, however, explain the similar genetic patterns in Oregon and Chile and hide higher levels of genetic diversity in the native range. In a study using allozymes, Kadono et al.  found genetically uniform populations of E. densa throughout Japan, but as in the case of isozymes, the technique yields a limited resolution compared to RAPDs and AFLPs.
To the best of our knowledge this is the first study of the genetic variation pattern of E. canadensis populations. In the congeneric invasive species Elodea nuttallii (Planchon) St John, both multiclonal  and monoclonal populations  were found in introduced ranges. In the Moder catchment (France), 2.7% AFLP polymorphism was detected in populations of E. nuttallii . A single introduction was hypothesised and the low level of variation that did exist was attributed to somatic mutations. Interestingly, two different mutants were found in two of the ten investigated populations and, like in our study, the UPGMA tree showed geographical structure in the distribution of genetic variation. Multiple introductions in NZ from Tasmania were discussed by Thomson  for E. canadensis. If this is correct, genetic diversity had to be very limited in the source populations, suggesting a stepping-stone model of invasion in NZ. We do not know the genetic pattern in Tasmania and how many source populations were involved. We can only move the discussion about the number of introductions from NZ to Tasmania. The differences with the Danish genotype suggest that higher levels of DNA variation are present within the species, but E. canadensis is invasive also in Europe and different evolutionary patterns could explain the divergence of allopatric gene pools.
Not knowing the genetic variation of these species in their native range, we cannot draw conclusions about the number of introductions to NZ (or Tasmania). Two possible scenarios emerge, however, from this study: multiple introductions of genetically similar genotypes, or one single founding event (consisting either of one genotype or a set of genetically similar genotypes) and evolution in situ by somatic mutations. The first scenario would entail either low genetic diversity in the native range or a stepping-stone model of colonization from other areas of the introduced range, as appears to be the case for E. canadensis. The second scenario, involving evolution of genetic diversity in NZ by somatic mutations is consistent with our results. A third model, which parsimoniously combines the previous two, limiting both the number of dispersal events and the number of mutations to have occurred in NZ, is that of ancestral polymorphisms retained in the three species .
Sources of genetic variation
Several results of this study indicate that evolutionary processes occurred after these species were introduced in the northern part of NZ's North Island. The measures of population differentiation show that the time elapsed since introduction is reflected in the genetic structure of the populations. Elodea canadensis was the first of the three species to be introduced in 1868 and its populations have higher Fst values and Nei's genetic distances than the later-established populations of E. densa and L. major. Also, the pattern of E. canadensis differs from that of the other species in showing more monophyletic groups, a continuum of genetic differences between individuals and populations, and differentiation between the geographically close populations of Taupo South and Otamangakau from the downstream locations. Strikingly the populations of Taupo South and Otamangakau were found to be a monophyletic group also in L. major, which was introduced in NZ as recently as in 1950. This can be explained either by recent "co-dispersal" of the two species (after 1950), or by independent dispersal histories shaped by the same geographic/physical constrains. In both cases multiple independent introductions appear very unlikely, as those would have blurred any common pattern. Considering that only one sex is present, or dominant, in each species, the absence of seeds and evident outcrossing events (recorded in the spectrum of pairwise genetic distances), somatic mutations seem to be a plausible source of genetic diversity in these clonal species.
The spectrum of pairwise genetic distances has previously been utilized to study genetic diversity in populations of clonal outcrossing plant species, as it may be helpful in distinguishing between genetic variation produced by somatic mutations and genetic variation due to outcrossing. The spectrum of clonal outcrossing populations of the marine submerged Posidonia oceanica (L.) Del.  shows a bimodal distribution, with a large peak at zero pairwise distance (α peak) indicating clonal reproduction, followed by decreasing frequencies in pairwise distances, due to somatic mutations. The second peak of the spectrum (β peak) is the mode of an almost normal distribution of frequencies in pairwise distances, which has been attributed to genetic diversity produced by outcrossing events. The same spectrum was obtained in outcrossing populations of the clonal tree Populus tremuloides Michaux . Compared to these studies, the spectra of L. major and E. densa populations show the same pattern that has been considered indicative of clonal reproduction and somatic mutations. Contrastingly, the spectrum of E. canadensis populations does not fit with this model. The normal distribution of pairwise differences points to outcrossing genotypes, whereas the limited range of polymorphism, which is comparable to that of E. densa, points to somatic mutations. The comparison with a genotype from Europe shows higher numbers of polymorphic fragments with all NZ genotypes. In addition if the spectrum was the result of outcrossing events between the NZ genotypes, outcrossing would be more frequent than clonal propagation, as the frequency of "zero" pairwise differences is very low, and seeds would be common in the populations. Seeds have, however, never been observed in E. canadensis in the northern part of NZ's Northern Island . However, the lack of β peak is not a conclusive evidence of absence of outcrossing. Sexual reproduction between clonal stands with the same or highly similar genotypes is not supposed to produce a β peak. Pairwise difference frequencies are also affected by somatic mutation rates as well as by population sizes at the time of introduction and at present, and by genetic diversity at the time of introduction. Several factors might interact in E. canadensis's spectrum, such as a pool of genetically similar/closely related founders, possible mutation-drift disequilibria and a longer introduction time.
Genetic diversity levels are different in the three species, in relation to the initial gene pools, possible ancestral polymorphisms, different somatic mutation rates and establishment times. Egeria densa, which in the North Island of NZ has the typical spectrum of a clonally reproducing species that has accumulated somatic mutations, has more genetic diversity than the other macrophytes. This makes E. densa more adaptable. In invasive populations of the clonal aquatic species Hydrilla verticillata (L. f.) Royle, Albrecht et al.  demonstrated that herbicide resistance evolved by somatic mutations.
In the absence of evident sexual reproduction, the distribution of genetic diversity in the populations documented in this study is found to be due to the dispersal of vegetative propagules, moderated by the presence of possible geographic/ecological barriers. The analysis of the geographic distribution of DNA polymorphic fragments showed more frequent dispersal events between neighbouring populations, even though long-distance dispersal was also common. Multiple introductions in lakes and rivers appeared also to be a recurring phenomenon, as well as down- and up-stream dispersal. The co-occurrence of more invasive species in the same localities and similarly complex dispersal routes in all three species suggest that human dispersal had a major role in the distribution of the genetic diversity. Johnstone et al.  ruled out bird-mediated dispersal because the distribution patterns of these species in NZ were not random in nature, but linked to fishing and boating activities. Considering that the populations sampled in this study were from a wide range of different habitats , dispersal opportunities combined with an empty niche  rather than suitable environmental conditions, explain the distribution of these species in the northern part of NZ's North Island, as also found by de Winton et al. . As discussed by Howard-Williams , NZ has no native canopy-forming submerged aquatic plants. Some kind of barrier seems, however, to limit recruitment and dispersal from Otamangakau and Taupo South from/to downstream populations in E. canadensis and L. major. Surprisingly, in L. major, these populations are isolated also from Lake Rotoaira, which is geographically close and connected by waterways to Otamangakau. A wider set of samples and populations covering also the southern part of the North Island and the South Island, combined with historic records of first introduction date in each location would help better understand the relationships between populations and reconstruct the introduction history of these species in NZ with higher resolution. It would also greatly enhance interpretation of nodes of dispersal vs. recruitment, providing a valuable tool for the local management of these aquatic weeds.
Very low levels of genetic diversity were found in three invasive aquatic species in the northern part of North Island, NZ. Even though it is not possible to quantify how much of the genetic variation can be attributed to each founding event, this study provides some evidence that evolutionary changes have occurred in the introduced range, even though sexual reproduction is not frequent or does not occur at all. Post-introduction evolution is supported by population genetic structure and similar phylogeographic patterns in E. canadensis and L. major. Considering the lack of seeds and the random dispersal of vegetative propagules, which appears to be human-mediated, somatic mutations are supposed to be a potential source of genetic diversity in these clonal species. However, this study does not provide direct evidence of such evolutionary events. Genetic variation should be analysed in the native populations to conclusively shed light on the evolution of these species in the North Island of NZ.
We sampled populations of the three species in a number of locations in the northern part of the North Island, NZ (Figure 9). This sampling area was chosen based on floristic and ecological records which indicate that all three species were established in this area at early stages of their introductions and from here their rapid spread was followed throughout the North Island . We focused on this region to test to what extent, in the absence of sampling across continents, a set of molecular data collected from a restricted geographic area can be informative about introduction history, and specifically the number of introductions. We used a sample of E. canadensis collected in Denmark as a reference to evaluate the genetic similarities of the NZ populations against a different genotype.
At each location three samples were collected from different macrophyte beds randomly chosen at an average distance of about three metres. As clonal propagation is the main (or exclusive) form of reproduction in these species in North Island, we considered a geographical extension of the sampling area more informative than an increased number of samples collected at each location. The term population is used in this study in a broader sense, which includes perennial clonal stands that are not necessarily in a gene flow relationship. From each specimen we sampled the top shoot and stored it in a sealed bag with silica gel. Samples from the same locations were considered representative of one population. In total 21 specimens of E. canadensis , representing 7 populations, 42 specimens of E. densa (14 populations) and 30 specimens of L. major (10 populations) were AFLP fingerprinted.
DNA was extracted with the E.Z.N.A. plant kit from the apical parts of shoots. DNA quality was checked on a 0.8% agarose gel, run for 1 h at 120V. DNA consisted of a sharp band of the size of about 20.000 bp compared to the Lambda DNA, Hind III marker 2 (MBI Fermentas) and no signs of DNA digestion were visible.
DNA concentration was measured with the Nano Drop Spectrophotometer ND-1000 (Saveen Werner) at 280 nm wavelength and was between 50 and 200 ng/μl in all samples, eluted with 50 μl E.Z.N.A. elution buffer.
DNA restriction and ligation
20 ng DNA were used for DNA restriction with 1.25 units each of EcoRI and MseI enzymes and ligation to 2.5 pmol EcoRI and 25 pmol MseI nucleotide adapters with 335 NEB cohesive end ligation units. Restriction and ligation were carried out simultaneously in a PCR (Peltier Thermal Cycler PTC-200 - MJ Research). The program was 37 ˚C for 4 h followed by 0.1 ˚C decrease in 2 h and 10 min at 70 ˚C. Restricted and ligated DNA was diluted 4x prior to pre-amplification.
2 μl of template DNA were added to 18 μl mastermix consisting of 10 μl 2x Mastermix (VWR Ampliqon), 6 picog EcoRI primer, 6 picog MseI primer and sterile water to reach the final volume of 20 μl. EcoRI primer and MseI primer consisted of one-nucleotide selective base. The PTC-200 PCR was programmed for 20 cycles, each with a 30 s DNA denaturation at 94 ˚C, 1 min primer annealing at 56˚C, and 1 min extension at 72 ˚C. Preamplified DNA was diluted 4x prior to selective amplification.
2 μl of template DNA were added to 18 μl mastermix consisting of 10 μl 2x Mastermix (VWR Ampliqon), 1 picog EcoRI primer, 6 picog MseI primer and sterile water to reach the final volume of 20 μl. EcoRI primer was Cy (fluorochrome) labelled. The PCR program was 94˚C for 30 s, 65 ˚C for 30 s decreased by 0.7 ˚C/cycle for the subsequent 12 cycles, 72 ˚C for 1 min, followed by 23 cycles at 94 ˚C for 30 s, 56 ˚C for 30 s and 72 ˚C for 1 min. Several primer combinations were tested and many did not show polymorphism. Three primer combinations were selected for E. canadensis (E-ACTcy+M-CTC, E-ATGcy+M-ACG, E-CGTcy+M-AGC) and E. densa (E-ACTcy+M-CTC, E-ATGcy+M-ACG, E-CAGcy+M-TAC) and four primer combinations for L. major (E-ACTcy+M-CTC, E-ATGcy+M-ACG, E-CGTcy+M-AGC , E-CAGcy-M-GCA) based on the presence of polymorphic DNA fragments and the scoring possibilities.
was run on a 7% acrylamide gel (Reprogel - Long Read) with 50-500 bp external sizers (GE Healthcare), in an ALF Express II DNA Analysis System (Amersham Pharmacia Biotech) at 1500 V, 55˚C for 400 min. 5 μl amplified DNA were added to 3 μl loading dye (GE Healthcare) and DNA was denatured in the PTC-200 PCR for 5 min at 94˚C prior to loading on the gel.
DNA fragments between 50 and 500 bp were scored for presence or absence with the program ALFwin Fragment Analyser Software package (Amersham Pharmacia Biotech). Only peaks clearly above the detection limit (set with a peak shape of 10 and a minimum height of 1%), well amplified and resolved in all samples were scored for polymorphism. The AFLP chromatograms were virtually identical within each species, with the exception of some samples in which a few peaks were absent (or, in a few cases, present) compared to the rest of the sample set. DNA was extracted, digested, ligated and amplified twice from these samples, to make sure that missing DNA fragments were due to polymorphism and not to DNA fragmentation. The complete reproducibility of AFLP chromatograms excluded possible ligation  and PCR  artefactual DNA fragments. A few samples of each species produced interrupted chromatograms and were excluded from the dataset. In total 102 DNA fragments were scored in 22 samples of E. canadensis , 127 DNA fragments were scored in 38 samples of E. densa and 142 DNA fragments were scored in 27 samples of L. major.
The scored polymorphic loci clearly showed either high peaks or no peaks. Low intensity peaks occurred in a very limited number of polymorphic loci and were scored as question marks. They corresponded to 1.5% of the peaks scored in E. canadensis, 1% of the peaks scored in E. densa and 0.7% of the peaks scored in L. major. These levels of ambiguity are comparable to or lower than those quantified by Bonin et al.  as typical systematic genotyping errors associated with the scoring of AFLP data. In E. canadensis nine polymorphic fragments, out of 22, had a frequency over 0.20 and one fragment had a frequency of 0.44. Polymorphic fragments were in most cases missing or present in all samples from the same population. In E. densa and L. major datasets only 3 and 1 DNA fragments respectively had a frequency over 0.20 and it was not possible to recognize any "population pattern" by scoring the gels.
The resulting binary matrix was analysed for each species with the program Arlequin ver. 3.11  to estimate the extent of genetic variation contained within and among populations and the extent of genetic differentiation of the populations. Question marks in the matrix were treated as missing data. AMOVA and population comparison test were based on pairwise differences and were tested respectively with 1000 and 100 permutations . The exact test of population differentiation, based on haplotypic frequencies, was calculated with a Markov chain of 100,000 steps and 10,000 dememorization steps . The same analyses were carried out between all NZ samples of E. canadensis, considered as one population, and the Danish genotype. Population differentiation was also evaluated based on Nei's  unbiased minimum genetic distances, which are limitedly affected by differences in sample size  and unbiased by small sample sizes . The genetic distances were calculated with the program TFPGA ver. 1.3, 2000 (Tools For Population Genetic Analyses; ). Question marks in the matrix were treated as missing data.
Genetic relationships among clones were calculated with PAUP ver. 4.0b10 (Phylogenetic Analysis Using Parsimony; ) and with Network ver. 188.8.131.52 Phylogenetic Network Constructions (Copyright 2004-2010 Fluxus Technologies Ltd.). PAUP NJ analysis were carried out based on both mean character difference in number of polymorphic fragments and genetic distances . Question marks were fitted by the program, either as present or absent fragments, in order to minimize tree length (lowest mean character difference or shortest genetic distance). Jack knife support was obtained with 37% character deletion  with 1000 replicates, "emulate jac-resampling" and random number seed. Bootstrap was set with 100 character resampling. The Danish genotype of E. canadensis was used as the outgroup for the NZ samples. For E.densa and L. major the NJ trees were calculated as unrooted phylograms.
The network of all maximum parsimonious trees was constructed with the reduced median algorithm . This algorithm, originally developed for binary matrices obtained by haploid sequence data, could be used for AFLP data because all characters could be entered with the same weight which is possible when the number of samples does not exceed 50. Question marks were processed by the program either as present or absent fragments to reach the shortest tree, estimated as lowest number of mutations. Using a parsimony criterion, the program introduces hypothetic missing haplotypes to the network, represented as median vectors (nodes).
We used the program TFPGA also to calculate UPGMA trees of the populations. Nei's genetic distances (unbiased minimum genetic distances) are based on pairwise common DNA polymorphic fragments and similarities between populations can be assumed to reflect a possible common vegetative origin and/or dispersal opportunities between populations. Statistical support was assessed with bootstrap analysis based on 1000 permutations and by changing the order of the samples several times in the data matrix, in order to alleviate the taxon entry-order problems associated with UPGMA method, as pointed out by Backeljau et al. .
- Localities abbreviations:
- HAM :
- HMU :
- KAI :
- McL :
- NGA :
- ORA :
- OTA :
- PAR :
- PON :
- ROA :
- ROM :
- ROT :
- Rout :
- RSM :
Rotoiti Sth. Man
- TAR :
- Tout :
- TIK :
- Tsth :
- SWA :
- WAI :
- WEA :
- WHA :
Mats H.G. Gustafsson is thanked for the critical reading of the manuscript and the valuable comments. The study was funded by the Danish Council for Independent Research, Natural Sciences via grants to TR and HB, and additional support from NIWA. We wish to thank the three reviewers who contributed with valuable comments to the final version of the manuscript.
- Lavergne S, Molofsky J: Increased genetic variation and evolutionary potential drive the success of an invasive grass. PNAS. 2007, 104: 3883-3888. 10.1073/pnas.0607324104.PubMed CentralView ArticlePubMedGoogle Scholar
- Geng Y, Pan X, Xu C, Zhang W, Li B, Chen J, Lu B, Song Z: Phenotypic plasticity rather than locally adapted ecotypes allows the invasive alligator weed to colonize a wide range of habitats. Biol Invasions. 2007, 9: 245-256. 10.1007/s10530-006-9029-1.View ArticleGoogle Scholar
- Ren MX, Zhang QG, Zhang DY: Random amplified polymorphic DNA markers reveal low genetic variation and a single dominant denotype in Eichornia crassipes populations throughout China. Weed Res. 2005, 45: 236-244. 10.1111/j.1365-3180.2005.00445.x.View ArticleGoogle Scholar
- Stebbins GL: Self fertilization and population variability in higher plants. Am Nat. 1957, 91: 337-354. 10.1086/281999.View ArticleGoogle Scholar
- Orive ME: Somatic mutations in organisms with complex life histories. Theor Pop Biol. 2001, 59: 235-249. 10.1006/tpbi.2001.1515.View ArticleGoogle Scholar
- Klekowski EJ: From Somatic mutation theory of clonality. The Ecology and Evolution of Clonal Plants. 1997, Backhuys Publication, Leiden: De Kroon H, Van Groenendael J, 227-242.Google Scholar
- Fischer M, Van Kleunen M: On the evolution of clonal plant life histories. Evol Ecol. 2002, 15: 565-582. 10.1023/A:1016013721469.View ArticleGoogle Scholar
- Salomonson A: Interactions between somatic mutations and plant development. Vegetatio. 1996, 127: 71-75. 10.1007/BF00054848.View ArticleGoogle Scholar
- Koppitz H, Kühl H, Kohl GJ: Some aspects of the importance of genetic diversity of Phragmites australis (Cav.) Trin. ex Steudel for the development of reed stands. Bot Acta. 1997, 110: 217-223.View ArticleGoogle Scholar
- Barrat-Segretain MH: Strategies of reproduction, dispersion and competition in river plants: a review. Vegetatio. 1996, 123: 13-37. 10.1007/BF00044885.View ArticleGoogle Scholar
- Chapman VJ: A history of the lake-weed infestation of the Rotorua lakes and the lakes of the Waikato hydro-electric system. NZ Dep scient ind Res Inf Ser. 1970, 78: 1-52.Google Scholar
- de Winton MD, Champion PD, Clayton JS, Wells RDS: Spread and status of seven submerged pest plants in New Zealand lakes. NZ J Mar Freshwat Res. 2009, 43: 547-561. 10.1080/00288330909510021.View ArticleGoogle Scholar
- Bowmer KH, Jacobs SWL, Sainty GR: Identification, biology and management of Elodea canadensis, Hydrocharitaceae. J aquat Plant Manage. 1995, 33: 13-19.Google Scholar
- Coffey BT, Clayton JS: New Zealand water plants: a guide to plants found in New Zealand freshwaters. 1988, Hamilton: Ruakura Agricultural Centre, New ZealandGoogle Scholar
- Thomson GM: The naturalisation of animals and plants in New Zealand. 1922, Cambridge, Cambridge University PressView ArticleGoogle Scholar
- Vos P, Hogers R, Bleeker M, Reijans M, Van De Lee T, Hornes M, Frijters A, Pot J, Peleman J, Kuiper M, Zabeau M: AFLP: a new technique for DNA fingerprinting. Nucleic Acids Res. 1995, 23: 4407-4414. 10.1093/nar/23.21.4407.PubMed CentralView ArticlePubMedGoogle Scholar
- Ward SM, Gaskin JF, Wilson LM: Ecological genetics of plant invasion: what do we know?. Invasive Plant Science and Management. 2008, 1: 98-109. 10.1614/IPSM-07-022.1.View ArticleGoogle Scholar
- Triest L: Isozymes in Lagarosiphon (Hydrocharitaceae) populations from South Africa: The situation in dioecious, but mainly vegetatively propagating weeds. Isozymes in Water Plants. Edited by: Triest L. 1991, Op. Bot. Belg, 4: 71-85.Google Scholar
- Carter MC, Sytsma MD: Comparison of the genetic structure of North and South American populations of a clonal aquatic plant. Biol Invasions. 2001, 3: 113-118. 10.1023/A:1014510730268.View ArticleGoogle Scholar
- Kadono Y, Nakamura T, Suzuki T: Genetic uniformity of two aquatic plants, Egeria densa Planch. and Elodea nuttallii (Planch.) St. John, introduced in Japan. Jpn J Limnol. 1997, 58: 197-203.View ArticleGoogle Scholar
- Vanderpoorten A, Lambinon J, Tignon M: Morphological and molecular evidence of the confusion between Elodea callitrichoides and E. nuttallii in Belgium and Northern France. Belg J Bot. 2000, 133: 41-52.Google Scholar
- Di Nino F, Thiébaut G, Muller S: Phenology and phenotypic variation of genetically uniform populations of Elodea nuttallii (Planch.) H. St John at sites of different trophic states. Fundam Appl Limnol, Arch Hydrobiol. 2007, 168: 335-343. 10.1127/1863-9135/2007/0168-0335.View ArticleGoogle Scholar
- Charlesworth D: Don't forget the ancestral polymorphisms. Heredity. 2010, 1-2.Google Scholar
- Rozenfeld AF, Arnaud-Haond S, Hernandez-Garcia E, Eguiluz VM, Matias MA, Serrao E, Duarte CM: Spectrum of genetic diversity and networks of clonal organisms. J R Soc Interface. 2007, 4: 1093-1102. 10.1098/rsif.2007.0230.PubMed CentralView ArticlePubMedGoogle Scholar
- Mock KE, Rowe CA, Hooten BM, Dewoody J, Hipkins VD: Clonal dynamics in western North American aspen (Populus tremuloides). Mol Ecol. 2008, 17: 4827-4844. 10.1111/j.1365-294X.2008.03963.x.View ArticlePubMedGoogle Scholar
- Albrecht M, Arias RS, Scheffler BE, Duke SO, Netherland M, Dayan FE: Somatic mutation-mediated evolution of herbicide resistance in the nonindigenous invasive plant hydrilla (Hydrilla verticillata). Mol Ecol. 2004, 13: 3229-3237. 10.1111/j.1365-294X.2004.02280.x.View ArticleGoogle Scholar
- Johnstone IM, Coffey BT, Howard-Williams C: The role of recreational boat traffic in interlake dispersal of macrophytes: a New Zealand case study. J Environ Manage. 1985, 20: 263-279.Google Scholar
- Riis T, Lambertini C, Olesen B, Clayton JS, Brix H, Sorrell BK: Adaptive strategies in invasive plants: Are phenotypic differences in three invasive aquatic plants caused by phenotypic plasticity or local adaptation?. Ann Bot. in press
- Howard-Williams C, Clayton JS, Coffey BT, Johnstone IM: Macrophyte invasions. Inland waters of New Zealand. DSIR Bulletin 241. Edited by: Viner AB. 1987, Wellington, 307-331.Google Scholar
- Howard-Williams C: Processes of aquatic weed invasions: the New Zealand example. J Aquat Plant Manage. 1993, 31 (special ed): 17-23.Google Scholar
- Baurens FC, Bonnot F, Bienvenu D, Causse S, Legavre T: Using SD-AFLP and MSAP to assess CCGG methylation in the Banana genome. Pl Mol Biol Rep. 2003, 21: 339-348. 10.1007/BF02772583.View ArticleGoogle Scholar
- Arens P, Coops H, Jansen J, Vosman B: Molecular genetic analysis of back poplar (Populus nigra L.) along Dutch rivers. Mol Ecol. 1998, 7: 11-18. 10.1046/j.1365-294x.1998.00316.x.View ArticleGoogle Scholar
- Bonin A, Bellemain E, Bronken Eidesen P, Pompanon F, Brochmann C, Taberlet P: How to track and assess genotyping errors in population genetics studies. Mol Ecol. 2004, 13: 3261-3273. 10.1111/j.1365-294X.2004.02346.x.View ArticlePubMedGoogle Scholar
- Excoffier L, Laval G, Schneider S: Arlequin ver. 3.0: An integrated software package for population genetics data analysis. Evol Bioinform Online. 2005, 1: 47-50.PubMed CentralGoogle Scholar
- Excoffier L, Laval G, Schneider S: Arlequin ver. 3.1 user manual 2006. [http://cmpg.unibe.ch/software/arlequin3/arlequin31.pdf]
- Nei M: Estimation of average heterozygosity and genetic distance from a small number of individuals. Genetics. 1978, 89: 583-590.PubMed CentralPubMedGoogle Scholar
- Gorman GC, Renzi J: Genetic distance and heterozygosity estimates in electrophoretic studies: effects of sample size. ASIH. 1979, 2: 242-249.Google Scholar
- Miller MP: Tools for population genetic analysis (TFPGA) 1.3: A Windows program for the analysis of allozyme and molecular population genetic data. 1997, Computer software distributed by authorGoogle Scholar
- Swofford DL: PAUP. Phylogenetic Analysis Using Parsimony (and other methods). Version 4. 1998, Sinauer Associates, Sunderland, MassachusettsGoogle Scholar
- Nei M, Li WH: Mathematical model for studying genetic variation in terms of restriction endonucleases. Proc Natl Acad Sci USA. 1979, 76: 5269-5273. 10.1073/pnas.76.10.5269.PubMed CentralView ArticlePubMedGoogle Scholar
- Farris JS, Albert VA, Källersjö M, Lipscomb D, Kluge AG: Parsimony jackknifing outperforms neighbor-joining. Cladistics. 1996, 12: 99-124. 10.1111/j.1096-0031.1996.tb00196.x.View ArticleGoogle Scholar
- Bandelt HJ, Forster P, Sykes BC, Richards MB: Mitochondrial portraits of human populations using median networks. Genetics. 141: 743-753.
- Backeljau T, De Bruyn L, De Wolf H, Jordaens K, Van Dongen S, Winnepenninckx B: Multiple UPGMA and Neighbor-joining trees and the performance of some computer packages. Mol Biol Evol. 1996, 13: 309-313.View ArticleGoogle Scholar
This article is published under license to BioMed Central Ltd. This is an Open Access article distributed under the terms of the Creative Commons Attribution License (http://creativecommons.org/licenses/by/2.0), which permits unrestricted use, distribution, and reproduction in any medium, provided the original work is properly cited.