Spawning in a threatened freshwater mussel shifts to earlier dates as a result of increasing summer mortality

ABSTRACT Freshwater mussels are among the most imperilled groups of animals on the globe, however, the drivers of mussel declines are still poorly understood. Here we show that in a seasonal

environment, _Unio crassus_ females can initiate spawning from late winter to late summer, implying a very high phenotypic plasticity of their spawning date. However, they shift their

reproductive effort to earlier dates and make greater investments in early broods in order to adapt to high spring temperatures and higher levels of summer mortality. Thus, the reproductive

investment during early spring may credit energy to be invested later in self-maintenance, in order to alleviate the impact of mortality. As a result, mussel reproduction is being

progressively compressed into earlier and shorter periods. Such constraints must reduce reproductive output and contribute to the decline of this already endangered group. The seasonal

pattern of reproductive effort can always serve as an excellent indicator of the conservation status of a given population. SIMILAR CONTENT BEING VIEWED BY OTHERS CHANGES IN LAKE STURGEON

SPAWNING PERIODICITY IS ASSOCIATED WITH PRIOR REPRODUCTIVE EFFORT Article Open access 30 January 2025 YEAR-ROUND SPAWNING OF THREE TROPICAL CYPRINIFORMES FISHES IN SOUTHEAST ASIA Article

Open access 02 June 2023 MULTIYEAR TREND IN REPRODUCTION UNDERPINS INTERANNUAL VARIATION IN GAMETOGENIC DEVELOPMENT OF AN ANTARCTIC URCHIN Article Open access 22 September 2021 INTRODUCTION

Although large freshwater mussels (Bivalvia, Unionida; hereafter, naiads) can dominate the benthic biomass of inland waterbodies and provide important ecosystem functions and services at a

very large scale1, they continue to be understudied. Moreover, recent mass die-offs have shown that they are in urgent need of conservation action2. Their rapid decline is both a worldwide3

and a European phenomenon4,5,6,7,8. The drivers of mussel declines are still poorly understood9, but the recent increases in the frequency and intensity of such declines point to a

relationship with global warming. The most widespread reaction to the global rise in temperatures has been the shift of phenology in seasonal environments, which is believed to be a simple

consequence of higher temperatures10. Thus, seasonal environments offer a climate credit11 to the species inhabiting them, reducing the impact of elevated temperatures, e.g. by their

starting reproduction at progressively earlier dates, thereby shifting reproduction to the cooler part of a season. In the case of naiads, it may be suspected that recent temperature rises

are coinciding with the mussels’ mortality. This has a negative effect on their demography and also exerts very severe selection pressure, the consequences of which are hitherto unknown. In

view of the abrupt nature of global temperature change, the only adaptation mechanism that seems to be keeping pace with the rate of global change is a high phenotypic plasticity, enabling

phenotypic adjustment12. However, although naiads are threatened at the global scale, hardly anything is known about their phenology, reproductive effort and natural history, not to mention

the plasticity of their life history traits. Critically, this knowledge is indispensable in the context of their monitoring and conservation2. Life history theory relates to the allocation

of energy to time, because the optimally time-distributed allocation of energy may reconcile many conflicting demands (e.g. current reproduction vs. future survival). In life history theory,

time is usually understood as a linear lifetime axis along which energy is allocated unevenly in order to maximize lifetime fitness13. But since resources fluctuate periodically in the

majority of habitats and these fluctuations have been amplified by global warming to levels threatening the survival of many species, it is essential to understand the energy allocations

within the course of particular seasons if one is to grasp the impact of phenology shifts on lifetime fitness14. Nevertheless, the patterns underlying seasonal allocations of energy and

their timing have not yet been explored, although a few important insights have been acquired15. To understand the mechanisms underlying the phenology of naiad reproduction, it is essential

to consider two reproductive strategies: (1) investment in a single brood, as seen in Anodonta species, and (2) investment in multiple, separate reproductive bouts occurring sequentially

throughout the spring and summer period, as observed in Unio species16. In the latter case, organisms theoretically have the potential to allocate resources differently across reproductive

bouts, necessitating an investigation into the extent of phenological plasticity. If such plasticity is absent, the ability to respond rapidly to environmental change is limited, making a

rapid shift in reproductive timing unlikely. To assess the possibility of phenological shifts, it is necessary to determine both the full range of dates when reproduction can be initiated

and the threshold beyond which further reproduction is no longer possible. For European naiads, the environmental cues that trigger the onset and cessation of reproduction remain largely

unknown. Current knowledge is restricted to general information indicating that reproduction occurs during the spring and summer months17. Moreover, data on reproductive investment across

the breeding season are scarce and very general18,19,20. A shift in reproductive phenology due to global warming could be advantageous if it results in an extended reproductive period due to

earlier initiation. If reproductive output in a given bout is constrained by factors such as body size, as observed in naiads21, yet available resources allow for further reproduction later

in the season, additional breeding bouts will occur to maximise resource utilisation within the seasonal reproductive window. This would enable individuals to produce more broods per

season, thereby increasing overall fitness22, Fig. 1A). Consequently, it can be hypothesised (H1) that an extended reproductive period, due to an earlier onset, is beneficial as it increases

the number of reproductive bouts within a season. However, the fitness benefits of shifting reproductive onset to earlier dates depend not only on the number of bouts but also on the level

of investment (i.e., the number of larvae) in each brood. Assuming an _ad libitum_ resource supply, the energy allocated to each reproductive bout should be equal, as it is limited primarily

by female body size21. If, alternatively, reproductive investment is proportional to the availability of organic, mostly algal food throughout the season23 and to increasing temperatures

that accelerate reproductive physiology24, then investment should be lowest at the beginning of the season, increase to a peak, and then decline (Fig. 1A). If reproductive investment is

empirically observed to be skewed towards earlier dates, it suggests the involvement of additional factors that override resource-based allocation strategies. Life-history theory predicts

that when mortality risk is high, organisms should allocate resources to reproduction earlier in life to maximise reproductive output before expected risk of death14. The same principle

should apply within a given reproductive season: an individual delaying reproduction until the following year faces a high probability of mortality before being able to reproduce again.

Consequently, the seasonal pattern of reproductive effort is expected to depend on the mortality risk pattern15,22. The most fundamental pattern is dictated by background mortality— the

constant, unavoidable risk of death due to predation, disease, or environmental hazards, irrespective of an individual’s condition or behaviour. Over time, these risks accumulate, leading to

an increasing probability of mortality as exposure duration lengthens. Assuming a linear relationship between mortality risk and time (i.e., decreasing survival probability over the

season), selection should favour immediate reproduction once resources and environmental conditions permit, as delaying reproduction increases the risk of pre-reproductive mortality22. Given

that mortality risk accumulates over time, individuals should allocate the majority of their energy at the beginning of the reproductive window, progressively reducing investment in each

subsequent breeding attempt as cumulative mortality risk increases. If the relationship between mortality and time increases sharply later in the season, then reproduction should not only be

concentrated at the onset of the reproductive period but should also terminate early when mortality risk becomes prohibitive. Under high mortality pressure, individuals should prioritise

self-maintenance over reproduction, ceasing reproductive activity before dangerous period (Fig. 1B). Thus, it can be hypothesised (H2) that the overall pattern of reproductive investment

across sequential reproductive bouts should be skewed towards earlier bouts and dates, while at high mortality rates, the reproductive period should be both early and shortened. To test

these hypotheses, the present study examines progeny production across consecutive spawning events and mortality rates in individually marked females of the thick-shelled river mussel, _Unio

crassus_ (Unionida, Bivalvia; Fig. 2A). This large freshwater mussel (reaching up to 7 cm in shell length) is long-lived, with a maximum lifespan of approximately 15–20 years, and inhabits

lotic environments across Europe17. _Unio crassus_ reproduces during the spring and summer months, although many aspects of its reproductive biology remain poorly understood. Like other

unionids, _U. crassus_ produces thousands of eggs, which are initially stored in modified demibranchs forming specialised brooding structures known as marsupia. The eggs develop into larvae

(glochidia), which remain in the marsupia for 10–35 days, with developmental rates dependent on ambient water temperature24. Once mature, the glochidia are released into the water, where

they attach to the gills and fins of host fish and after a period of encystment, they detach from the host and settle into the benthic environment25. Due to its rapid population decline in

recent decades, _Unio crassus_ is classified as Endangered (EN) on the IUCN Red List and is protected under EU regulations and national conservation laws26. RESULTS In the four rivers (Fig. 

2B), spawning was initiated by different females during almost the entire breeding season: in different years the spawning initiation period lasted from 53 to as many as 104 days (70 days on

average, col. 5 in Table 1). If all the subsequent spawning events are included, the total breeding period lasted from as early as mid-March (after the ice melt) to as late as early August,

i.e. from 61 to 132 days (105 days on average; col. 7 in Table 1). The maximum number of spawning events of an individual during one reproductive season varied between the rivers from no

more than 3 in the Warkocz to 7 in the Biała (average 2.28, SD = 3.635). Among the 551 females that were examined in all rivers and in all seasons, just 49 were found which had not spawned

during a given season. Each particular breeding attempt of the same female could differ in the volume of glochidia filling the marsupium (Fig. 2C-E). The earlier the first spawning event,

the more broods raised during the season (Fig. 2F-I; Table 1, col. 8, except the Warkocz in 2019, when spawning ended very early). In the early spawning events, the marsupia were completely

filled with larvae (Fig. 2C), whereas later in the season, the proportion of the marsupium volume filled with larvae (Fig. 2D-E) decreased (Fig. 2J-M). The general trend in marsupial filling

across all rivers was negative over the course of the season. With each subsequent brood, the log-transformed percentage of marsupium filling decreased significantly (GLMM Model no. 1:

estimate = − 0.088, SE = 0.014, _p_ < 0.001; for details of statistical models, see Methods), corresponding to an approximate decrease of 8.4% per brood. Similarly, in relation to time

within the reproductive season, the log-transformed marsupium filling decreased significantly with each passing day following the first brood (GLMM Model no. 1: est. = −0.0024, SE = 0.00052,

_p_ < 0.001), corresponding to an estimated 0.24% decline per day. The combined effect of the number of spawning events and their total volume also decreased significantly during the

season (Fig. 2N-R for data pooled for given river, Table 1., col. 9 for particular seasons), although an exception was found in the lowland river Czarna (Table 1, see also Fig. 2K and O).

Every season and in all the rivers, spells of adult mortality occurred during late spring and early summer (grey bars in Fig. 2F-I). Of 76 females that died, 60 (79%) had not spawned at all

during the season when they died, 8 had spawned once, 1 had spawned twice and 7 had spawned three times. Female mortality was the highest in the Warkocz (39%), then the Biała (27%) and the

Czarna (26%), whereas it was noticeably lower in the San (21%; see also Table 2). Background mortality ceased at the end of the breeding season (late June, Fig. 2F-I), which however, do not

exclude massive die-offs during mid-August (2019, the San – unpubl. data). The overall difference between spawning and death dates in reference to the first spawning date in given river were

highly significant: the Md of 1st spawns occurred on 26th day since the first spawn, whereas the Md date of death date was 42 days later (GLMM no. 2: estimate = -0.85, SE = 0.061, P < 

< 0.001). Pairwise comparisons of the results of GLMM model no. 3 showed the following log-transformed differences between spawning and death: the Biała river (est. = −0.93, SE = 0.140,

_p_ < 0.001), the Czarna (est. = −0.72, SE = 0.236, _p_ = 0.0022), the San (est. = −0.66, SE = 0.078, _p_ < 0.001), and the Warkocz (est. = −1.36, SE = 0.131, _p_ < 0.001). The

largest difference was observed in the Warkocz, indicating a longer temporal separation between spawning and death in this river compared to others. Significant differences in events timing

between rivers were also observed: events occurred significantly later in the San compared to the Biała (est. = 0.29, SE = 0.080, _p_ < 0.001) while events in the Warkocz were marginally

earlier (est. = −0.18, SE = 0.109, _p_ = 0.089) compared to the Biała. The interaction between event type and river was significant in the Warkocz (est. = 0.42, SE = 0.191, _p_ = 0.026),

confirming that the difference between spawning and death timing was greater in this river. The variance of the random effect for river was negligible, suggesting that most variability was

captured by the fixed effects. In 2019, the Warkocz, Czarna and San were monitored in parallel. Separate Generalized Linear Models were used to assess differences in spawning and death

timing across these rivers in 2019. In the reference to spawning timing GLMM model no. 4 revealed significant differences between rivers, with spawning occurring later in the San (est. =

0.52, SE = 0.121, _p_ = 0.0001) and earlier in the Warkocz (est. = −0.45, SE = 0.143, _p_ = 0.0055) compared to the Czarna. The largest difference was observed between the San river and the

Warkocz (est. = 0.97, SE = 0.125, _p_ < 0.0001). In contrast, the death timing model (GLMM model no. 5) showed no significant differences between rivers (_p_ > 0.05). Post-hoc

comparisons confirmed that death timing was consistent across the Czarna, San, and Warkocz, with no significant pairwise differences observed (_p_ > 0.49). The death timing appears to be

more consistent, in comparison to spawn dates (Fig. 3A). A GLMM model no. 6 revealed significant differences in the timing of spawning and death events in the San River. Overall, death

occurred significantly later than spawning (est. = 0.39, SE = 0.170, _p_ = 0.022), with significant interactions between event type and season (Fig. 3B): spawn vs. death dates differed

significantly in 2016 (est. = -1.35, SE = 0.599, _p_ = 0.024), in 2018 (est. = -1.39, SE = 0.369, _p_ = 0.0002) and in 2019 (est. = 0.39, SE = 0.170, _p_ = 0.022), however no significant

differences were found for 2017. The largest temporal separation between spawning and mortality was found in 2018, and in 2016, although then the number of dead mussels was low; while in

2017 events were more synchronous, also showing this tendency in 2019. The disproportionately high mortality in the San river in 2019 coincided with temperature extremum (Fig. 2C) in

comparison to other years. The differences between the median date of the first spawning events (Table 2, col. 3) and the median date of mussel deaths (col. 4) found in particular seasons

and rivers yielded time windows of very different lengths (col. 5). The window length correlates with the proportion of spawning females (col. 6, rs = 0.88, N = 10, P = 0.002) and the number

of their broods not influenced by mortality before glochidia release (col. 7, rs = 0.96, N = 10, P < 0.001). It is clear that in many years, all or almost all the glochidia could have

been released before the onset of the mortality period (e.g. the Warkocz river). On the other hand, the ratio of the reproductive effort within a window to the total reproductive effort

(col. 10) indicates that if spawning is postponed, there is an inversely proportional risk of the spawn being lost if the female dies. The length of the time window (col. 5) correlates

negatively with the relative decrease in reproductive investment (col. 12) due to female mortality in a given year (rs= -0.86, _N_ = 10, _P_ = 0.001). In other words, the more intense the

selection related to lost reproduction investment in late spawning events, the shorter the time window for safe spawning. If one assumes that an average female spawns 364% of marsupium

volumes during a season (mean for col. 9) and has a mean probability of death of 15% (mean for col. 11), then 8% of glochidia, on average, will be affected by the female mortality period

(mean of col. 12), which reflects current phenotypic selection against late spawning. DISCUSSION In the four _Unio crassus_ populations studied between 2015 and 2021, females initiated

spawning from late winter to late summer, demonstrating a high degree of phenotypic plasticity in spawning timing. Instances of both late initiation of the first spawning event and very late

subsequent spawnings indicate that neither low winter nor high summer temperatures entirely prevent reproduction. This suggests that spawning is physiologically feasible throughout the

season, even when the marsupium is filled to its maximum capacity with larvae (see Fig. 2K). These findings support Hypothesis 1, which predicts that earlier breeding facilitates a greater

number of reproductive bouts within a season. However, the data also indicate that mussels do not follow the theoretically advantageous pattern of increasing reproductive investment in

response to improving environmental conditions over the season (Fig. 1A). Instead, investment per reproductive bout declines significantly both across sequential broods of individual females

and over time within the season. This declining investment may be explained by background mortality, which was recorded in each river during every breeding season. Notably, mortality never

occurred prior to the spawning period. While, at the level of an individual, death obviously cannot preclude reproduction, at the population level, it is plausible that mortality could be

particularly intense after winter, preventing early reproductive investment. However, this was not the case in the studied populations. Instead, mortality occurred during the breeding

season, meaning its probability accumulated over time. Consequently, to minimise the risk of mortality before reproducing, most individuals should allocate the majority of their reproductive

energy at the beginning of the reproductive window, reducing investment in each subsequent reproductive bout. This pattern is consistent with Hypothesis 2, although further, long term

research is needed both to confirm and clarify the underlying mechanisms. Studies on reproductive effort in Unio species remain scarce, with most literature providing only general

descriptions of reproductive timing (e.g. 17,20). The only exception is the work of Hohwald19, who first reported that _U. crassus_ females do not always produce sufficient glochidia to

completely fill their marsupia. Hohwald also documented that _U. crassus_ produces multiple broods per season, reporting “up to five spawning events”. Theoretically, repeated handling of

mussels could artificially increase the apparent number of reproductive bouts, for instance, by inducing brood loss through stress or disturbance. However, experimental tests of handling

effects conducted in the Biała and San rivers24, under different disturbance regimes (biweekly, weekly, and every other day), showed that only the highest disturbance frequency (every other

day) induced miscarriage of broods. Even under these conditions, miscarried orange conglutinates were clearly visible in the water, and brood loss was evident from disruptions in glochidial

developmental stages. Since no such patterns were observed in the present study, handling effects are unlikely to have influenced our results. From a theoretical perspective22, the observed

decline in reproductive investment was attributed to increasing mortality risk. However, alternative explanations remain possible. One particularly plausible factor is the capital vs. income

breeding strategy27. A recent study20 on related species _U. tumidus_ reported that individuals resorb resources from the gonads in December, likely as an adaptation for somatic maintenance

during winter. This may explain how these mussels can initiate spawning very early in the season, even in the absence of food availability. However, such capital-stored resources may be

insufficient to sustain late-season breeding, leading to a progressive decline in reproductive investment as pre-winter energy reserves are depleted. Nevertheless, _U. tumidus_ in the

studied population maintained continuous gametogenesis throughout the year (a pattern also observed in _U. crassus_, based on our own unpublished data). Despite this, _U. tumidus_ does not

reproduce early; instead, spawning and glochidial release occur in June–July, which supports an income breeding strategy rather than capital breeding20. We examined only four rivers, which

limited our ability to directly test the relationship between individual reproductive investment and background mortality. However, even within these four populations, clear patterns

emerged. In the Warkocz river, which exhibited the highest mortality, spawning was significantly advanced compared to the other rivers, with reproduction initiated well before major

mortality events, suggesting stronger selection for early reproduction. Additionally, reproductive investment was highly restricted or even ceased entirely in later broods. By contrast, in

the San River, where mortality was lowest, the breeding season began later, spawning frequently overlapped with mortality events, and reproductive investment in late broods remained high.

According to the theory of energy allocation13,14,28,29, energy investment in self-maintenance has absolute priority over investment in reproduction and growth. This principle is

particularly important in long-lived organisms such as freshwater mussels. Producing one or two additional broods in a given summer may significantly increase short-term reproductive

success, but it also exposes individuals to a higher mortality risk, potentially jeopardising dozens of future broods over a 20-year lifespan. This trade-off explains why reproductive

investment is often divided into multiple smaller broods, particularly in warm conditions where rapid larval development allows individuals to fine-tune their reproductive timing before

mortality risk escalates. This self-maintenance may also explain why 49 females in the study completely refrained from reproduction and died later in the season. The primary driver of

mortality in 2019 appears to have been a large-scale environmental factor, as spawning dates varied significantly between rivers, whereas mortality dates were nearly identical across all

sites. Although formal statistical testing was not possible, the coincidence of mortality events with the unprecedented June 2019 heatwave (which had no analogue in the 70-year European

temperature record 30) suggests that elevated temperatures exerted a large-scale impact. The effect of temperature on mortality may be direct (e.g. via reduced oxygen availability) or

indirect, such as by increasing susceptibility to disease31. A physiological threshold may also limit early-season spawning shifts. In high-mortality rivers, spawning began immediately after

ice melt, when water temperatures exceeded 5 °C24. However, at such low temperatures, larval development takes at least three times longer than in late spring. In extreme cases, development

may fail to reach completion32. Thus, even if selection favours earlier breeding, physiological constraints may prevent a corresponding shift in the first spawning event. The predicted rate

of climate warming may not alter this mechanism: a 10 °C increase in winter temperatures (e.g. from − 10 °C to 0 °C) will not reduce the 5 °C developmental threshold, whereas a 10 °C

increase in spring or summer temperatures (e.g. from 15 °C to 25 °C) could be lethal for mussels33. This progressive shortening of the reproductive window may explain high interannual

variation in recruitment in unionids34, a hypothesis that requires further testing. In conclusion, in the studied populations _Unio crassus_ exhibited high flexibility in spawning timing,

allowing for earlier initiation, increased spawn number, and thus enhanced reproductive success. However, energy investment per brood declined progressively over the season, likely due to

high late-spring mortality selecting for earlier reproduction. Further research is needed to directly test the trade-off between reproductive investment and self-maintenance costs to assess

its demographic consequences for _U. crassus_ populations. METHODS Data were collected in 2015–2021 in four rivers (southern and central Poland; Table 1, Fig. 2B): two mountain rivers, i.e.

the San (studied in 2015–2019, 49°11’50.1”N 22°40’ 56.8E, 544 m asl) and the Biała (2015–2016; 49°51’37.9 N, 21°02’3.3E, 228 m asl), and two lowland ones, i.e. the Warkocz (2019 and 2021;

50°50’25.0”N, 20°45’27.0”E, 258 m asl) and the Czarna (2019; 50°56’50.0”N, 19°50”59.0E, 200 m asl). All four rivers harbour big populations of _U. crassus_, with recent recruitment and large

densities. All four rivers are protected by the Natura 2000 network and are included in the state system of monitoring in accordance with the EU Habitats Directive. All were evaluated as FV

(favourable). The San River is a perennial mountain river located in the Eastern Carpathians, southeastern Poland. It is one of the major tributaries of the Wisła (Vistula) River, flowing

for 457 km and draining a catchment area of approximately 16,861 km². At the study site near Procisne village, the river has a relatively straight channel, approximately 50 m wide, with

shallow waters (0.3–0.7 m depth). The discharge at low water levels is approximately 5–6 m³/s, with seasonal variations influenced by snowmelt and rainfall. The river channel along the study

reach remains entirely natural, with high water quality, low nutrient levels, and minimal pollution. This is due to the river drains the Bieszczady National Park, a strictly protected area

with almost no anthropogenic impacts. The riverbed is predominantly composed of gravel and exposed rock, while fine sediments accumulate along the banks, supporting herbaceous vegetation,

mainly _Carex_ species. The surrounding catchment is dominated by mixed forests, with minor contributions from grasslands. The Biała River is a perennial river in the Western Carpathians

(southern Poland) and forms part of the Vistula River basin. It flows for 96 km from the Beskid Mountains to its confluence with the Dunajec River, draining a catchment of approximately 940 

km², which is predominantly covered by mixed forests, meadows, and agricultural fields. At the study site, the channel remains natural, featuring a gravel bed approximately 14 m wide,

incised 2–3 m into a fine sediment floodplain. The river follows a pool-riffle sequence, with low water depths ranging from 0.1 to 1.5 m and a discharge of approximately 2–2.5 m³/s at low

water levels. The banks are overgrown with Salix species, while the floodplain supports degraded riparian forests near the riverbed, with meadows dominating the remaining landscape. Water

quality is mesotrophic. The Warkocz River is a perennial stream in the Świętokrzyskie Mountains, a highland region in central Poland. It flows for 17.5 km, draining a 54 km² catchment of

forested and agricultural landscapes before joining the Lubrzanka River, which ultimately flows into the Vistula River. At the study site, the river has a naturally meandering channel, 5–10 

m wide, incised approximately 2 m into fine sediments. The riverbed is composed of sandy substrate with gravel patches in riffles. The depth varies considerably, ranging from 10 cm in

riffles to 1–1.5 m in pools. The banks are overgrown with alder (Alnus species), while the floodplain supports alder-dominated forest near the riverbanks, with meadows covering the remaining

area. No data are available on water quality or discharge. The Czarna River is a perennial, lowland, meandering river in central Poland, flowing for approximately 47.5 km and draining a 637

 km² catchment before joining the Pilica River, a left-bank tributary of the Vistula. The river flows through a flat lowland landscape, incising approximately 2 m into fine sediments. At the

study site, the river retains a natural channel, with a width of approximately 10 m and a depth of 0.7–1 m at low water levels. The riverbed consists primarily of sand, with the presence of

large woody debris and marginal vegetation dominated by _Sparganium_ species. The floodplain is covered with meadows and pastures. Approximately 4 km upstream, a large fish pond influences

local hydrology, though its exact impact on the study site remains unquantified. In each of the four rivers, a random selection of mussels was collected in very early spring, just after the

ice melt. Then, ca. 130 individuals of the dominant size class (ca. 5 cm long, except in the river Czarna, where the dominant size was ca. 6–7 cm), were individually marked with an

alphanumeric code engraved on the periostracum, sexed by gonad puncturing to find sperms or oocytes, then released back into the river at the same site from which they had been taken, but

grouped together to facilitate finding them again. The marsupia of female mussels were inspected every 10–14 days (weekly in the Biała River in 2015–2016). The percentage of marsupium volume

filled with larvae (Fig. 2C–E) was estimated visually. To assess the developmental stage of the larvae, the marsupia were punctured using a thin needle, and the contents were examined in

situ under a field microscope24. During each inspection, females were typically sampled twice to verify that the developmental stages of the glochidia in consecutive samples were consistent

with the established developmental sequence of brooding glochidia (morula, blastula, …, D-shaped, …, snapping-open glochidium with a protruded larval thread). This method enabled precise

determination of the laying date in early-season broods, when larval development proceeds slowly enough to allow for age estimation in days24. After examination, mussels were immediately

returned to the water. The total number of broods raised per season was then determined for each female, and the cumulative volume of marsupium filled with larvae was estimated across all

broods. The number of individuals for which the total marsupium volume was estimated was lower than the number of individuals analysed for brood count (Table 1, columns 8 and 9). Individuals

were excluded from volume estimation if there was any uncertainty regarding the completeness of their broods, for example suspected miscarriage, partial glochidia release, or any

inconsistencies in glochidial developmental stages between consecutive inspections, which could indicate that larvae developed and were released within a period shorter than the inspection

interval. For analysing the impact of temperature on mortality in the San (Fig. 3C.), temperature data for the Solina reservoir, in the upper course of the San, were used. These data were

obtained from the State Institute of Meteorology (SIM) and are publicly available at https://danepubliczne.imgw.pl/data/dane_pomiarowo_obserwacyjne/dane_hydrologiczne/miesieczne/. The

reservoir water temperature was selected as it effectively averages the temperatures of the San’s numerous tributaries, including that of the study site, and is less susceptible to local

fluctuations or short-term disturbances. Thus, it provides a representative measure of large-scale thermal conditions, responding only to significant climatic or hydrological changes.

STATISTICS To account for differences in study years across rivers, if not stated otherwise, in all GLMM models dates of spawn and death were standardized as the number of days since the

first female spawn in a given year and river. Because data were collected in different years in different rivers the coding enabled the use of data from all rivers and all years in the GLMM

analyses. A Gamma distribution with a log link function was used to model the skewed distribution of coded dates. The results of GLMM models were reported on the log scale and transformed to

the original scale where necessary for interpretation. All statistical modelling was performed in R4.4.2., simple statistics were computed using Statistica 13.1. We applied a generalized

linear mixed-effects model (GLMM, model no 1.) to analyse the factors influencing reproductive investment in mussels, measured as the percentage of marsupium fullness. The model used a

Tweedie distribution with a log-link function to accommodate the positively skewed distribution of the data and the high frequency of values near the upper bound (100%). The fixed effects

included brood sequence number and the number of days since the first brood in a given river in given year to assess sequential and temporal patterns in reproductive investment. Random

effects were specified to account for hierarchical data structure, including variation between rivers and between individual mussels nested within rivers. Model parameters were estimated

using the glmmTMB package, which is optimized for Tweedie-distributed responses. Model diagnostics were performed using the DHARMa package to assess residual patterns and model fit. To

evaluate the general difference in timing between spawning and death events across all rivers, a Generalized Linear Mixed Model (GLMM, model no 2.) was employed, including event type

(spawning or death) as a fixed effect and river as a random intercept to account for river-level variability. This approach allowed for the estimation of an overall difference between

spawning and death dates. To analyse differences in the timing of spawning and death within each of the rivers, a model GLMM No 3. included fixed effects for event type (spawning or death),

river, and their interaction (type × river). River was also included as a random effect to account for variability between rivers. Due to the limited number of repeated measures across

individual mussels within rivers, the inclusion of individual ID as a random effect led to issues with model convergence and overparameterization. Excluding individual ID ensured a

parsimonious model that could be reliably estimated, while river-level random effects accounted for variability between rivers. Post-hoc pairwise comparisons of spawning and death timing

within each river were conducted using the Tukey adjustment for multiple comparisons. Estimated marginal means (EMMs) were derived from the model to assess these contrasts. All above

analyses were performed using the lme4 package for GLMMs and emmeans for post-hoc comparisons. Because the table of data is not orthogonal (Table 1), whereas all three rivers (the Czarna,

San, Warkocz) were studied in 2019, this allows to compare the differences between rivers without influence of different seasons. Moreover, 2019 was a year with exceptional mortality (Fig. 

3C), which specifically predestine this year to be studied. To analyse the differences in spawning and death timing between these rivers, we applied separate Generalized Linear Models

(models No 4 and 5) for each event type (spawning and death). The response variable was the date of the event, transformed into the number of days since the earliest recorded event in the

dataset. The fixed effect in both models was river, modelled as a categorical variable. Pairwise comparisons between rivers were performed using Tukey-adjusted post-hoc tests. Statistical

analyses were conducted using the glm function for model fitting and the emmeans package for post-hoc comparisons. To analyse differences in the timing of spawning and death events across

seasons in the San river, a Generalized Linear Mixed Model (GLMM, model No 6) was applied. The response variable was the relative timing of events within each season, calculated as the

number of days since the first observed event in that season. The fixed effects included event type (Spawn or Death), season, and their interaction. Individual ID was included as a random

effect to account for repeated measures within individuals. Post-hoc pairwise comparisons between Spawn and Death were conducted within each season using the Tukey adjustment for multiple

comparisons. Analyses were performed using the lme4 and emmeans packages. DATA AVAILABILITY The datasets generated during and/or analysed during the current study are available from the

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supported partly by LIFE+ project “LIFE4delta” LIFE17-NAT_PL_000018, funded by the European Union and partly by statutory funds of the Institute of Nature Conservation, Polish Academy of

Sciences. The study was conducted on the basis of permits Nos. WNP.6401.190.2014.RN-2, WNP.6401.1.117.2016.ŁL.2, WNP.6401.88.2019.JSz.2, WNP.I.6401.30.2019.AD, OP-I.6401.168.2014.MMr,

OP-I.6401.163.2016.MMr and DZP-WG.6401.78.2021.TŁ, granted to study a protected species (_U. crassus_). ). Kacper Zając gave some useful tips about R. AUTHOR INFORMATION AUTHORS AND

AFFILIATIONS * Institute of Nature Conservation, Polish Academy of Sciences, 31-120 Kraków, Al. Adama Mickiewicza 33, Kraków, Poland Tadeusz A. Zając & Katarzyna Zając Authors * Tadeusz

A. Zając View author publications You can also search for this author inPubMed Google Scholar * Katarzyna Zając View author publications You can also search for this author inPubMed Google

Scholar CONTRIBUTIONS while both K.Z. and T.Z. contributed equally to this work, T.Z. took the leading part in data analysis and writing the manuscript. CORRESPONDING AUTHOR Correspondence

to Tadeusz A. Zając. ETHICS DECLARATIONS COMPETING INTERESTS The authors declare no competing interests. ADDITIONAL INFORMATION PUBLISHER’S NOTE Springer Nature remains neutral with regard

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earlier dates as a result of increasing summer mortality. _Sci Rep_ 15, 7733 (2025). https://doi.org/10.1038/s41598-025-91926-9 Download citation * Received: 21 October 2024 * Accepted: 24

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