As an effect of the advancing breakdown of biogeographic barriers, the introduction of alien invasive species is ranked among the main drivers of biodiversity loss (Sala et al. 2000; Clavero and García-Berthou 2006; Millennium Ecosystem Assessment 2005; Copp et al. 2014a, b), and homogenization of ecosystems (Rahel 2002). Invasive alien species (IAS) have often caused irreversible damage (Jackson et al. 2002; Keller et al. 2011), eliciting severe ecological, economic and social impacts (Gherardi et al. 2009; Mazza et al. 2014a). The lack of geographical barriers (Lodge 1993), the specifically high intrinsic dispersal ability of aquatic organisms (Ricciardi and Rasmussen 1999; Beisel 2001) and extensive human influence make freshwater ecosystems particularly prone to biological invasions (Havel et al. 2015).

The North American crayfish Procambarus clarkii is considered a highly invasive species (Henttonen and Huner 1999; Huner 2002) that has been intentionally introduced (Holdich 1999, 2016) throughout the world in the twentieth century (Lodge et al. 2012). The European invasion by P. clarkii began with an introduction to Spain in 1973 for aquaculture purposes (Souty-Grosset et al. 2016). The species has steadily spread across Europe, becoming abundant in Portugal, Spain, France and Italy. It was originally introduced to increase crayfish harvests (Souty-Grosset et al. 2006), but it is currently traded also for ornamental purposes (Mazza et al. 2015). Procambarus clarkii is a successful coloniser in Europe (Souty-Grosset et al. 2016), quickly establishing in new and different environments. It is listed among the 100 worst invasive species in Europe (Pyšek et al. 2011), and among the species of unional concern under the new EU Regulation 1143/2014 regarding alien invasive species. Procambarus clarkii, widespread in freshwater and even brackish ecosystems (Scalici et al. 2010; Souty-Grosset et al. 2016), has been recently reported to also colonise cave ecosystems (Mazza et al. 2014b). It exhibits a wide range of impacts through predation, competition, bioaccumulation and increased eutrophication, and pathogen and disease transmission (Barbaresi and Gherardi 2000; Angeler et al. 2001).

The ability to exert heavy impacts, while being tolerant to diverse environmental conditions, makes the species able to completely transform habitats, thus giving P. clarkii the role of an ecosystem engineer (sensu Jones et al. 1997). The species is considered a tertiary to secondary burrower (Gherardi 2000; but see also Ilhéu et al. 2003), i.e. digging burrows to withstand environmental extremes periods (e.g. drought) and during reproductive periods (Gherardi and Barbaresi 2000; Gherardi 2006; Souty-Grosset et al. 2014). It can thus overcome unfavourable conditions in the invaded habitat (Souty-Grosset et al. 2016). Its burrowing activity is known to vary according to soil particle size, water cycle and structure of land as well as to damage agricultural and natural systems, causing channel bank erosion (Fig. 1), increase of water turbidity and fine sediments (Huner 1977; Anastácio and Marques 1997; Holdich 1999; Rodríguez et al. 2003; Correia and Ferreira 1995), significant physical modification (Barbaresi et al. 2004; Orlandini et al. 2015), and reduction of plant density (Souty-Grosset et al. 2014). Moreover, burrowing animal species have been identified as one of the main causes for levee failures (Chang and Lange 1967; Rudnick et al. 2000; Gribsholt et al. 2003; Serre et al. 2008; Hanson et al. 2010) causing floods (Fig. 1) and damage in excess of $500 million in Italy (Orlandini et al. 2015). In Italy, crayfish burrowing activity has already damaged about 30% of partially human shaped irrigation canals with huge costs for management authorities (F. Gherardi in Lodge et al. 2012).

Fig. 1
figure 1

a Typical burrows produced by Procambarus clarkii on irrigation ditches; b due to the burrowing activity of Procambarus clarkii broken levee alongside the river Secchia (Emilia Romana, Italy)

Previous studies have investigated the burrowing behaviour of invasive crayfish outside their native range (Correia and Ferreira 1995; Kouba et al. 2016), but only a very few have directly quantified burrow morphology and related this directly to damage of river banks and/or levees (e.g. Guan 2010; Consumi 2016).

Behaviour of crayfish in invaded habitats can differ from that in the native range. For example, the signal Crayfish (P. leniusculus) is considered to be a non-burrowing species in its native North American range but commonly burrows in riverbanks of invaded habitat in England (Guan 2010). Mating between male and female P. clarkii usually occurs before females start to burrow (Huner and Barr 1991). Females hold eggs and rear juveniles in the burrow but the extent of male participation in the construction and defence of the burrow remains unexplored. Hence, the aim of the present work is to assess the burrowing activity of P. clarkii, analyse the structure of the constructed burrows and the behaviour displayed by male and female crayfish to identify possible differences between sexes.


Structure of burrows

In spring 2016, 80 specimens of P. clarkii were collected in local ponds in northern Tuscany (Central Italy) using baited traps. Cephalothorax lengths (CL) were measured using a Vernier calliper (accuracy: 0.01 mm) and then labelled (numbers and letters) on the cephalothorax using a white marker. The specimens were maintained in plastic containers (12.5 × 22.5 × 13 cm; water level: 3 cm; weekly water change) for the entire duration of this study in the laboratory of the Department of Biology, University of Florence, under a natural light/dark cycle at room temperature (range 17.1–25.7 °C) and fed with carrots. Carrots are commonly used to feed P. clarkii under laboratory conditions as they are considered as an ideal food source due to the diet spectrum of mature P. clarkii and carotenoids sustaining its natural red colouration (Huner and Meyers 1979; Gherardi et al. 2013). Three days before the start of each experiment, specimens were moved in the same plastic containers to DICEA (Department of Civil and Environmental Engineering, University of Florence) laboratory. Mature adult specimens with cephalothorax length comprised between 36 and 46 mm (average length: 44.5 ± 3.1 mm) were selected, being the individuals of this size the most active (in terms of mobility) and frequent in natural environments (Gherardi et al. 2000). For each replicate, two couples were formed, composed of size-matched (maximum difference CL: 5–6%) male and female, and, after each replicate, were not used for further experiments. To minimize bias in the experiments, only individuals in good condition without mutilations were selected. From April to August 2016, ten independent replicates of the experiment were conducted, each in five-day cycle using artificial model levees simulating Italian irrigation canals built at laboratory of DICEA. The experimental soil granulometry (composed of 61% silt, 21.7% sand, 17% clay and 0.3% gravel) is particularly favourable to crayfish burrowing activity (Barbaresi et al. 2004) and is typically used by local Basin Authorities for the construction of levees in many areas colonized by this species in Tuscany. The scale of the constructed levee was a 1:1 copy (same size as levees in the field) of levees that can be frequently found along ditches (Fig. 1), the most commonly invaded habitat by P. clarkii.

The levee was constructed in a static water tank (L: 300 cm; W: 96 cm; H: 110 cm) during 3 days prior to the 5-day cycle of each experimental replicate. It was built by laying multiple soil layers (5–8) of approximately 10–12 cm height on top of each other with the first one being rectangular shaped (100 × 96 × 10 cm) and each consecutives layer decreasing in size. All layers, except the bottom one, were compacted using a common dynamic loading procedure whereby soil was regularly hit by a given weight of about 15 kg from a height of about 20 cm. The first day and before laying soil layers, portions of hydro-expanding bentonite (waterstop) were attached to the glass sides and middle section of the tank bottom to prevent preferential water pathways along the contact surfaces. The completed levees had a trapezoidal shape over a wider rectangular basal layer, total height was 50 cm and length 100 cm (Figs. 2, 3).

Fig. 2
figure 2

Model of the artificial levee used for the experiment at DICEA (Department of Civil and Environmental Engineering, University of Florence)

Fig. 3
figure 3

Constructed model levee at DICEA (Department of Civil and Environmental Engineering, University of Florence) 48 h after release of crayfish into the setup

Before each replicate, water level (at room temperature) was set to 25 cm on one side to cover 50% of the levees height and maintained constant during the experiment; this level gave the possibility to observe the burrowing behaviour of crayfish in the levee. A barrier was put on top of the levee to exclude movements of crayfish from the waterside to the empty side. On the first day of each replicate (after the 3 days to build the model), two pairs of size-matched crayfish were placed into the water and the experiment was video-recorded for 96 consecutive hours. During night-time, light was provided by a halogen lamp covered with a blue filter simulating “moon light”, enabling observing animal movements without disturbance. Air and water temperature were recorded during all the experimental replicates and controlled as best as possible but were subject to fluctuations due to the different climatic conditions occurring during the study period. At the end of the replicate, crayfish were baited out of the burrows using cat food. Then, water was removed from the tank and from the burrows, using a syringe and a rubber pipe if needed. Polyethylene foam was inserted into the burrows while applying pressure on the entrance to ensure that the foam could expand inside the burrow. To be sure that every burrow was filled with foam, the levee was taken down carefully, injecting more foam in instances when empty burrows were uncovered. After the entire structure was taken down, the foam structure was placed in the empty and cleaned tank to take pictures (Fig. 4). The total excavated volume was measured by submerging the foam structure in a volumetric water bowl. The maximum length (longest tunnel) of each burrow, the maximum and minimum diameter of each tunnel at its beginning, middle and end section were also measured to generate a single mean diameter value per tunnel. The presence, diameter and volume of each chamber (enlarged structure which significantly differs from the tunnel; Gherardi 2000) as well as the presence of multiple openings were assessed.

Fig. 4
figure 4

Reconstructed model of the levee after the experiment, showing the position of burrows and the excavated volume of burrows

Behavioural parameters

The following parameters were recorded from the camera placed in a 90° angle over the levee-front and analysed for each individual: (1) latency in seconds (time until crayfish started burrowing after being placed into the setup); (2) time in seconds spent in different behaviours, such as “burrowing” (i.e. visible active digging into the soil on the external surface of the levee), “burrow protection” (i.e. standing directly in or above the burrow edge), “horizontal movement” (i.e. movement under the water level on top of the first rectangular layer of the levee), “outside movement” (i.e. movement outside of the water line), and “breathing” (i.e. the typical sideway position used in this species to breath air oxygen outside the water, see Holdich 1999). When animals were in the burrow, no activity could be recorded.

Statistical analyses

Data were tested for normality by applying the Shapiro–Wilk’s test (p > 0.05), skewness and kurtosis z-values (− 1.96 to + 1.96) and displaying the data distribution using histograms, normal Q–Q plots and boxplots. Data on burrowing latency did not meet assumption of normality and were analysed in relation to sexes, using a Mann–Whitney-U test. Burrow latency, burrow length, excavated volume and air temperature were analysed with Spearman correlations. To test whether one sex started new burrows significantly more often than the other, Chi square (χ2) test was applied. Following the statistical approach by Gherardi et al. (2011), a two-way repeated measures multivariate analysis of variance (MANOVA; statistic: Wilk’s Lambda Λ) was applied to all the behavioural parameters using sex and day/night as factors after assumptions of multivariate normality were controlled with quantile–quantile (Q–Q) plot and met. MANOVA was followed by univariate tests for between-subject’s effects.

Using the data from all the experiments, time spent in each behavioural pattern was compared between day and night (Wilcoxon-signed-rank-test, statistic: W), and between sexes (Mann–Whitney-U-test, statistic: U). Moreover, behaviours of males and females were analysed separately between day and night (Wilcoxon-signed-rank-test, statistic: W). For replicate #5 no video data were obtained due to a technical error in the camera setup. The level of significance under which the null hypothesis was rejected is α = 0.05. Text and figures give mean values ± standard errors (SE) or median values (+ 1° and 3° interquartile). SPSS®, Statistical Package for Social Science 13.0 for Windows was used for the statistical analyses.


Structure of burrows

Overall, 17 burrows were constructed by 40 crayfish during the ten experiments. In seven replicates, levees contained two burrows with three openings (n = 4) and two openings (n = 3). In the remaining three replicates, levees had only one burrow with two openings and in two cases burrows with only one opening (Table 1). During ten replicates and out of 17 burrows, only five replicates contained chambers (n = 6) which were constructed directly at the end of the entry tunnels with two having partially constructed tunnels outgoing from it (Fig. 4).

Table 1 List of total numbers of burrows and entries constructed by crayfish during ten replicates plus information of occupation of burrows by crayfish at the end of each replicate

Mean size of chambers (n = 6) was 15.8 ± 5.2 (height) × 11.4 ± 2.5 (width) × 10.9 ± 1.3 (depth) cm and had a mean volume of 0.9 ± 0.6 dm3. The average length of the excavated tunnels was 50.2 ± 32.4 cm (ranging from 7.0 to 123.6 cm) with a mean perimeter of tunnel sections of 17.9 ± 2.4 cm (ranging from 14.1 to 21.6 cm). Diameter of tunnels (n = 17) was shown to be between 4.8 ± 0.9 cm and 6.0 ± 1.0 cm. The excavated volume on the total levee volume showed a mean of 1.9% ± 0.9% (0.00528 m3; 5.0256 l) with 1.0% (0.0024 m3; 0.24 l) being the smallest and 4.0% (0.011 m3; 10.9 l) the largest percentage of excavation. In seven replicates, crayfish were found to occupy burrows in couples of one female and one male (Table 1). Additionally, in various replicates one pair of crayfish constructed a complex burrow while the other pair constructed a shorter and simpler structure (Tables 1, 2).

Table 2 Description of excavated structures (chambers and tunnels) during the experiments performed

Behavioural parameters

In seven cases, the establishment of couples (i.e. both sexes starting burrowing together without fighting and protecting the burrow against other individuals) was observed after 5100 ± 1452 s. No correlation was found between latency time and burrow length (rs = 0.25, n = 7, p = 0.589), latency time and excavated volume (rs = 0.452, n = 7, p = 0.260), burrow length and excavated volume (rs = − 0.43, n = 7, p = 0.337), air temperature and latency time (rs = − 0.71, n = 7, p = 0.071), temperature and burrow length (rs = 0.19, n = 7, p = 0.602). Overall, males and females started constructing burrows with the same frequency (χ2 = 1.17; n = 13; p = 0.279; females: n = 8; males: n = 5), also in case of the first burrow (n = 4 for both sexes). Both sexes did not significantly differ for latency time (U = 15, n = 8, p = 0.06; male: 740 s, 486–1862 s; female: 3281 s, 1536–8036 s). The time spent in each behaviour (Fig. 5) was found not to correlate with neither air nor water temperature (rs = − 0.38 to 0.30; n = 9, p always > 0.05). The MANOVA revealed no statistical significance for interaction of factors (Λ = 0.11, df = 5.28, p = 0.99) and single factor (sex: Λ = 0.67, df = 5.28, p = 0.65; time: Λ = 1.39, df = 5.28, p = 0.28) for the considered behavioural parameters. The univariate analysis after MANOVA showed only a difference in the burrowing activity for time, with crayfish spending more time during the day rather the night (F = 5.206, df = 1, p = 0.03; other parameters: F: 0.001–3.417, df = 1, P: 0.981–0.076). Comparisons of the total time spent by males and females in different behaviours at night or during the day showed an increased burrowing activity and horizontal movements during the day (Table 3). In contrast, no significant difference in the total amount of time spent in the different behaviours was observed between males and females (Table 3).

Fig. 5
figure 5

Total time spent in each behaviour (%) through the nine replicates. Left y-axis: % of each behaviour, right y-axis: maximum air temperature measured during each experiment

Table 3 Comparisons between sex and day time, within sex and within day time for each behavioural parameter, using Mann–Whitney-U test [U] or Wilcoxon-signed-rank test [W]


In several countries, the damage to levees caused by crayfish like P. clarkii’s burrowing activity is noteworthy, due to the increased vulnerability to floods (Chang and Lange 1967; Souty-Grosset et al. 2016; Consumi 2016) and leakage from irrigation canals (Fishar 2006; Orlandini et al. 2015). Here, the burrow structure of typically in Italy constructed levees (Orlandini et al. 2015; Condicelli 2016) is described, and the behaviour of Procambarus clarkii associated with the construction of burrows in an artificially environment is analysed (but see also Kouba et al. 2016). The results showed that crayfish promptly started digging and that both sexes are involved in burrowing activity. These data are thus important to increase the knowledge of P. clarkii biology and could help develop levee structures that are less vulnerable to the presence of P. clarkii under consideration of burrow structure (Kouba et al. 2016).

Structure of burrows

In the present study, two types of burrows were observed: (1) complex burrow with entrances at the water line commencing straight into the levee (Fig. 6a, c) and in some cases with a central chamber, which volume can contribute to almost 50% to the overall excavation volume of the burrows, and (2) a considerable number of short burrows constructed u-shaped and placed near the ground in the first basal layer of the levee (Fig. 6b), as described by Holdich and Lowery (1988). While some variation between experimental and natural conditions are possible, obtaining similar data from the field is very difficult due to inaccessibility of levees. However, due to the simulation of similar conditions (no vegetation, presence of water, 50–50 sex ration, comparable densities), results presented in this study are likely to be expected under natural conditions. However, the overall low level of variation (only two types of burrows) was likely due to the constant water level (Holdich and Lowery 1988; Ilhéu et al. 2003) and the experimental setup, but is in agreement with previous studies that also reported complex and simple burrow structures (Correia and Ferreira 1995; Ilhéu and Bernardo 1996; Gherardi et al. 2002) with similar burrow opening diameters (Souty-Grosset et al. 2014), with a burrow depth ranging from 0.28 to 0.58 m (Portugal: Correia and Ferreira 1995).

Fig. 6
figure 6

Reconstructed model of the levee after the experiment, showing the position and the excavated volume of burrows. a, b Observed burrows as positioned inside the levee; c frontal view of the model levee after water has been removed showing both types of typically constructed burrows: the straight into the levee dug burrows near the water line and the “u-shaped” burrows near the ground.; d model of all differing types of burrow structures observed during the experiments, a: complex structure with chamber, b: “u-shaped” burrow, c: blind tunnel commencing straight in the levee

In contrast to the horizontally burrows constructed at 0–20 cm below the water level, previously described burrows showed a simpler morphology, with usually one opening at a distance of 0–10 cm above the water surface enlarging in a tunnel with a terminal chamber, potentially with muddy plugs or a chimney reaching up over the burrow opening. These were generally occupied by two mature crayfish (Jaspers and Avault 1969; Correia and Ferreira 1995) as observed in ten out of 17 constructed burrows in the present study. From field observations conducted in July 2017, three out of seven burrows had a chamber (P. Haubrock, pers. comm.). In Europe, burrows can be inhabited by about 4.8 younger individuals, on average (Correia and Ferreira 1995), while in the native area by up to 50 individuals (Huner et al. 1984). We found that the ultrastructure of constructed chambers was overall consistent with previous described structures (Jaspers 1969; Huner and Barr 1984; Correia and Ferreira 1995; Ilhéu and Bernardo 1996). On the contrary, Souty-Grosset et al. (2014) observed more complex burrowing activity in dry fishponds, with burrows having also mud plugs. Besides water level, morphology, slope and structure of levee could have influenced the type of burrows constructed in the present study.

Generally considered as a “secondary burrower” in its native area, this species spends most of its life outside of burrows, retreating into them for reproduction, and to avoid predation or dehydration. However, this species often seems to be considered as a “secondary to tertiary burrower” (depending on whether the author considers burrow usage or burrow structure; Hobbs and Hart 1959; Holdich 1999) in invaded area, due to its ability to shift its behaviour according to the different environments (Souty-Grosset et al. 2014). Hence, it is likely that burrowing behaviour, burrow structure and use of burrows differ among invaded areas due to differing particle size and water cycle (Souty-Grosset et al. 2014) as well as location of burrow (ground vs. levee, Condicelli 2016; Solari et al. 2016).

Although the experimental setup was not suited to analyse the different burrow types under dry conditions (vertical and submerged burrows—see Gherardi et al. 2002), two different types of burrows were produced. As stated by Barbaresi et al. (2004) and Correia and Ferreira (1995), apart from the presence of rocks that seemingly decrease the burrowing activity (Souty-Grosset et al. 2014), sediment composition, presence of vegetation and water availability affect the structure of constructed burrows.

This becomes obvious, as (i) shelter (i.e. rocks, structure) would provide additional cover and reduce burrowing activity, (ii) too small or large particles would increase the difficulty of burrow-construction (Barbaresi et al. 2004; Solari et al. 2016), and (iii) vegetation (and the roots within the sediment) affect the porosity of the sediment (Ilhéu et al. 2003; Souty-Grosset et al. 2014). Additionally, Kouba et al. (2016) showed that P. clarkii is capable of constructing different burrow structures in response to environmental changes, directly increasing its survivability. In the present study, burrow structures were generally either “u-shaped” (Gherardi 2000) or, likely due to the availability of constant water levels, similar to secondary burrower burrow morphologies but horizontally with more complexity (Fig. 6), usually expected from “primary burrowers” (Hasiotis and Mitchell 1993; Holdich 2002; Gherardi et al. 2002). While the typical “u-shaped” burrow could be “tertiary”, providing suitable for short time protection under low construction effort, the more complex “secondary burrow” morphologies may be advantageous (aeration, additional exit) and suitable for longer refuge. Nonetheless, considering the present experimental setup and the reproductive phase of this species in Italy overlapping with the time of the study, it is not clear why in various experiments only one pair of crayfish constructed a larger, more extensive burrow, while the other pair remained constructing the previously mentioned u-shaped burrow. While a lack of space is possible, interactions between couples as well as different responses to the experimental setup (directly constructing a more permanent shelter vs. trying to get shelter fast) are probable.

The recorded burrowing activity led to a total amount of excavation up to 4% of the levee volume (with a high percentage of the excavated volume contributed by the chambers), that can directly affect levee stability and alter the seepage process by shortening filtration pathways with consequent possible collapse of the levee (Consumi 2016; Solari et al. 2016). Since the constructed model levee was a reproduction of typically irrigation canal levees, a damage and threat to the stability of levees similar to that ones we observed in the laboratory can be hypothesized for levees in nature, considering that the number of burrows increases over time (Barbaresi et al. 2004).

In order to avoid cannibalism and aggressive interactions, the density used in the experiment was low (four crayfish per m2). Moreover, according to the Catch Per Unit Effort values found in field studies (e.g. > 20: Aquiloni et al. 2010; Cecchinelli et al. 2012) or densities used in semi-natural studies to quantify species impact (8 m−2: Gherardi and Acquistapace 2007), higher abundances of P. clarkii are possible. However, the general layout (shape and granulometry) simulated model levees in Italy, as they are usually not covered in vegetation and free of structure, offer low to no shelter in surface waters (Figs. 4, 6), reproducing the burrowing activity observed in invaded habitats. Because burrow density is stated to be independent from crayfish density (Barbaresi et al. 2004; Tricarico et al. 2010), 4% of excavation by four individuals seems low, but the estimated percentage relates to 96 h. With increasing time and potentially higher densities of P. clarkii, the probability of levee breaches as well as collapses increases (Condicelli 2016). Also, collapsing river banks are only one issue, while the creation of holes through irrigation ditches and related damage of the construction can lead to water leakage and shortage of water in irrigation canals for agriculture (Orlandini et al. 2015). Therefore, the excavation of 4% during 96 h can be considered as a high impact.

However, an intense immediately starting burrowing activity was always recorded in all the experiments, highlighting the considerable impact especially since P. clarkii tends to rebuild rather than reuse older burrows. Periodically changing of water level, due to the use of local waterways for irrigation and associated water cycle during summers, leads to a consistent annual fluctuation (water present between late autumn and spring, dried conditions during summer) and might induce an increased digging activity with a high impact on levee stability in times of drought, especially due to the presence of chambers as observed in this study, but ad hoc experiments are necessary to solve this issue. On the contrary, the constant shallow water level used in the experiments likely results in several shorter and horizontally constructed burrows (Gherardi et al. 2002) that will have a delayed effect on levees.

Behavioural parameters

Burrows were generally occupied by a couple composed by a male and a female as previously observed by Holdich and Lowery (1988). In the absence of shelter, both males and females began burrowing rapidly. Both sexes started digging, with similar latency time, and thus males did not initiate burrowing to induce mating. The observed data however, enable speculation of a trend towards a decrease in latency time under an increase in temperature, highlighting the more active pattern and the possible relation to the reproductive phase (Daniels et al. 1994). Indeed, in Tuscany species reproduction usually occurs between June and July when females need a burrow (Gherardi et al. 2002). In this study, mating was not observed outside the burrow, but rather a protective guarding of females by males that immediately approached advancing other P. clarkii while both were constructing the entry of the respective burrow (P. Haubrock, pers. obs.). The rapid pairing of P. clarkii in male–female couples and subsequent cooperative burrowing suggests several interesting hypotheses. For instance, it could be to induce mating but P. clarkii typically mates in open water before burrowing, and if it was to induce mating males would have initiated burrowing, but this was not the case. Since mating was never actually observed, it could just be that crayfish cooperated with burrowing to get underground (into shelter) more quickly as hypothesised for Cambarus hartii (Helms et al. 2013a). However, P. clarkii always collaborated in teams of one female and one male, leading to support that it was related to mating.

Additionally, both sexes displayed burrow protection, e.g. guarding outside the burrow entrance from other crayfish, and sharing the burrowing itself, indicating that before the mating, both contribute to these tasks. Helms et al. (2013a) found, that in artificial burrowing setups, multiple individuals of C. hartii initially shared burrows as a mean to get underground, but, nonetheless, burrowing activity was not shared equally.

Overall, no differences were observed between males and females (Gherardi et al. 2002), and both sexes alternatively worked at the same burrow, equally participating to burrowing activity. Kouba et al. (2016) inserted P. clarkii in a situation of drought and forced to construct typical vertical burrows. In this study, it was found that burrows constructed by both male and female P. clarkii differed from previous studies, in that they were constructing no plugs and burrows were horizontal rather than vertical. In our study a more visible burrowing activity on the levee was observed during the day. However, it is not possible to affirm that crayfish always dig more during the day, because the activity inside the burrows was not visible, even if this is in part indirectly supported by the less frequent horizontal movements observed during the night and the observation of freshly produced tunnels after nights.


Our study showed the extent of burrowing behaviour of the invasive P. clarkii in an artificial setup and, in contrast to previous studies (e.g. Huner et al. 1984 and Huner 2002 for an overall summary), revealed how similar female and male crayfish are for burrowing activity. Considering the used experimental procedure, the observed excavation values of maximum 4% are likely an underestimation, especially because in the field a higher abundance of crayfish is present, and the number of burrows increases over time. Moreover, levees are generally not vegetated and affected by other environmental pressures (e.g. loss of stability and integrity due to scarce maintenance). Our results indicate how burrowing activity (considering the extent of horizontal burrows as well as crayfish reconstructing rather than reutilizing burrows) can possibly reduce the levee stability, underlining the pressure exerted by P. clarkii in invaded habitats. Additionally, P. clarkii is considered a warm water species, but its distribution in Europe and high tolerance towards low temperatures suggest its overwintering and reproduction in colder areas for which the observed burrows structures are an advantage. Possibilities to decrease the behavioural effects of P. clarkii on levees should be addressed in the future.