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Freshwater salinization and the evolved tolerance of amphibians

Wiley
Ecology and Evolution
Authors:

Abstract

The increasing salinization of freshwaters is a growing environmental issue as a result of mining, agriculture, climate change, and the application of de‐icing salts in regions that experience ice and snow. Due to narrow osmotic limits, many freshwater species are particularly susceptible to salinization, but it is possible that repeated exposures over time could favor the evolution of increased salt tolerance. Using collected nine populations of larval wood frogs ( Rana sylvatica ) as eggs from ponds and wetlands with close proximity to roads and spanning a wide gradient of salt concentrations. In the first experiment, we used a time‐to‐death experiment to examine the salt tolerance. In a second experiment, we examined whether population differences in salt tolerance were associated with trade‐offs in growth, development, or behavior in the presence of control water or a sublethal salt concentration. We found that populations collected from ponds with low and intermediate salt concentrations exhibited similar tolerance curves over a 96‐h exposure. However, the population from a pond with the highest salt concentration exhibited a much higher tolerance. We also found population differences in growth, development, and activity level among the populations, but these were not associated with population differences in tolerance. In addition, the sublethal concentration of salt had no impact on growth and development, but it did cause a reduction in tadpole activity across the populations. Collectively, these results provide further evidence that some species of freshwater organisms can evolve tolerance to increasing salinization, although it may only occur under relatively high concentrations and without trade‐offs in growth, development, or behavior.
Ecology and Evolution. 2024;14:e11069. 
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1 of 10
https://doi.org/10.1002/ece3.11069
www.ecolevol.org
Received:11December2023 
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Accepted :13Decemb er2023
DOI: 10.1002/ece 3.11069
RESEARCH ARTICLE
Freshwater salinization and the evolved tolerance of
amphibians
Rick Relyea| Brian Mattes | Candace Schermerhorn | Isaac Shepard
This is an op en access arti cle under the ter ms of the CreativeCommonsAttribution License, which permits use, distribution and reproduction in any medium,
provide d the original wor k is properly cited.
©2024TheAut hors.Ecology a nd Evolutio n published by John Wiley & So ns Ltd.
Depar tment of Biological Sciences,
Rensselaer Polytechnic Institute, Troy,
NewYork,USA
Correspondence
Rick Relyea, Dep artment of Biological
Sciences, Rensselaer Polytechnic Institute,
Troy,NewYork12180USA.
Email: relyer@rpi.edu
Funding information
Directorate for Biological Sciences,
Grant /AwardNumber:DEB16-55168;
Rensselaer Polytechnic Institute
Abstract
The increasing salinization of freshwaters is a growing environmental issue as a
resultofmining,agriculture,climatechange,andtheapplicationofde-icingsaltsin
regions that experience ice and snow. Due to narrow osmotic limits, many fresh-
water species are particularly susceptible to salinization, but it is possible that re-
peated exposures over time could favor the evolution of increased salt tolerance.
Using collected nine populations of larval wood frogs (Rana sylvatica) as eggs from
ponds and wetlands with close proximity to roads and spanning a wide gradient
of salt concent rations. In the fir st experiment , we used a time-to-de ath experi-
ment to examine the salt tolerance. In a second experiment, we examined whether
populationdifferencesinsalttolerancewereassociatedwithtrade-offsingrowth,
development, or behavior in the presence of control water or a sublethal salt con-
centration. We found that populations collected from ponds with low and interme-
diatesaltconcentrationsexhibitedsimilartolerance curvesover a96-hexposure.
However, the population from a pond with the highest salt concentration exhibited
a much higher tolerance. We also found population differences in growth, develop-
ment, and activity level among the populations, but these were not associated with
population differences in tolerance. In addition, the sublethal concentration of salt
had no impact on growth and development, but it did cause a reduction in tadpole
activity across the populations. Collectively, these results provide further evidence
that some species of freshwater organisms can evolve tolerance to increasing salin-
ization, although it may only occur under relatively high concentrations and with-
outtrade-offsingrowth,development,orbehavior.
KEYWORDS
amphibian, evolution, microevolution, sensitivity, toxicology
TAXONOMY CLASSIFICATION
Ecotoxicology, Evolutionary ecology
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1  | INTRODUCTIO N
The salinization of global freshwaters is a global issue with contribu-
tions from mining, agriculture, saltwater intrusion from sea level rise
and storm surge events linked to climate change, and the application
ofde-icing salts on roads in regions that experience snow and ice
(Dugan et al., 2017; Hintz & Relyea, 2019). Indeed, more than 18
millionmetrictonsofde-icingsaltsareappliedtoroadsintheUnited
States each winter (Jackson & Jobbágy, 2005). Much ofthese de-
icing salts wash into adjacent freshwater habitat s (Corsi et al., 2010;
Dugan et al., 2017 ), which has myriad ecological consequences for
aquatic s pecies, communi ties, and ecosys tems (Hintz & Relyea , 2019;
Schuler et al., 20 19). During the past decade, scientists have taken
an “evolutionary toxicology ” approach to better understand how
freshwater organisms respond to salinization (Bickham, 2011; Brady
et al., 2017). This is especially true as evolution via natural selec-
tion to anthropogenic changes on contemporary timescales in other
conservation contexts has gained greater appreciation (Stockwell
et al., 2003; Kinnison et al., 20 07).Indeed,evolvedtolerancetode-
icing salts has been demonstrated in various taxonomic groups in-
cluding zooplankton, (Coldsnow & Relyea, 2018; Hintz et al., 2019)
and aquatic macrophytes (Bora et al., 2020). However, it remains to
beseenwhethertheabilitytoevolve toleranceto de-icingsaltpol-
lution is common among freshwater organisms.
Given their narrow osmotic range (Boutilier et al., 1992), and sensi-
tivity to chloride (Brad y, 2012; Sanzo & Hecnar, 2006) amphibians have
been of par ticular interest to scientists trying to understand the abilit y
ofo rg anis ms toad ap ttothecontinuings tre ssofd e-ic in gs al tp ollution.
Moreover, as amphibians are in decline globally (Stuart et al., 2004),
understanding their ability to adapt to contaminants such as salts has
important conservation implications (Blaustein & Bancroft, 2007 ).
Some evidence suggests that it is possible for amphibians to evolve
increased tolerance to high salt concentrations where they have likely
livedinbrackishhabitatsforcenturies(Gomez-Mestre&Tejedo,2003;
Hopkins & Brodie, 2015). However, freshwater salinization is a much
morerecentphenomenon,particularlyinregionswherede-icingsalts
havebeen increasinglyappliedtoroads sincethe 1940s. Asaresult,
wetlands closer to roads can contain 20 times more salt than wetlands
far from roads and these high salt concentrations can have substan-
tial negative effects on the survival of amphibian embryos and larvae
(Sanzo & Hecnar, 2006; Karraker et al., 20 08; Brady, 2012; Petranka &
Francis, 2013; Hill & Sadowski, 2016).
One amphibian species that has received growing research atten-
tion is the wood frog (Rana sylvatica), which has a geographic range
that spans much of the eastern continental U.S. and Canada over to
Alaska.Wood frogsare anexcellentstudy speciesbecausethey are
explosive breeders, which results in populations throughout a region
all breeding within the same week. This synchronized breeding behav-
ior allows researchers to directly compare populations that are living
in wetlands that vary widely in salinity. In past studies in Connecticut
(USA), wood frog larvae that were collec ted as eggs from ponds
with high salt concentrations exhibited lower sur vival (Brady, 2013,
2017 ), slower growth and development (Forgione & Brady, 2022), and
reduced larval activity (Brady et al., 2022; Hall et al., 2 017) compared
to conspecific populations collected as eggs in wetlands far from
roads. These studies have suggested that wood frogs are maladapted
to salinization. However, other studies of wood frogs in Vermont
(USA)havefoundthatpopulationscomingfromhigh-saltwetlandsdo
not differ in survival, but have superior locomotor performance, adult
mass, and fecundit y, suggesting adapt ation rather than maladapt ation
(Brady et al., 20 19).Population-leveladaptiontohigh-saltconcentra-
tions has also been observed in a species of salamander in roadside
ponds ( Ambystoma maculatum; Brady, 2012), but contradictory results
werefoundinshort-termlabstudies(Bradyetal.,2017).
It currently remains unclear what conditions seem to favor the
evolution of adaptation versus maladaptation to salinization. Most
studies showing maladaptation to salt have compared wood frog pop-
ulations living in wetlands close to roads to wood frog populations
living in wetlands far from roads (Brady, 2013, 20 17). However, close
proximit ytoroads(e.g.,within50 m,wheresaltconcentrationsareel-
evated; Karraker et al., 2008) may present additional selective forces
(e.g., other pollutants) that may affect how populations are able to
evolveadaptationsormaladaptat ionstosalt.Analternat iveapproach
would be to compare populations collected from wetlands that vary
widely in salt concentration but are all in close proximity to roads.
In addition to examining adapt ations and maladaptations to sa-
linization by examining survival when exposed to lethal concentra-
tions, it is also important to examine life history traits (e.g., growth,
development) and behavior when animals are exposed to sublethal
salt concentrations (Brady et al., 2022). This is particularly interesting
when consideringpotential trade-of fsof evolved tolerance, where
we might hypothesize that increased tolerance comes at the cost of
slower growth, slower development, or impaired behavior. For exam-
ple, wood frog populations can evolve tolerance to pesticides at the
expense of parasite resistance (Billet et al., 2021; Hua et al., 2017 ).
To understand how amphibians may be evolving to salinization,
we conducted two experiments using nine wood frog populations
from wetlands that were all in close proximit y to roads but differed
widely in their salt concentrations. The first experiment tested the
hypothesis that populations living in wetlands with high salt concen-
trations have evolved higher salt tolerance. The second experiment
tested the hypothesis that populations that have evolved the highest
salt tole rance will exp erience tra de-of fs of slower grow th, slower
development, or impaired behavior.
2  |METHODS
2.1  | Animal collection
We collected newly oviposited wood frog egg masses from nine road-
sid epondsinupstateNewYork,US Athatvariedi ntheirchloride con-
centrati ons at the time o f egg collec tion, ran ging from 1 to 744 mg
Cl/L (Figure 1). Given that salinity ef fect s tend to diminish beyond
50 m(Karraker et al., 2008), all pondswere lessthan 40 m from the
nearest road. During April 6–12, 2022,we gathered tenpartial egg
   
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masses(i.e.,approximatelyone-fourthofamass)fromeightsitesand
seven partial masses from one site where only seven masses were
laid.Weplacedthepartialeggmassesin350-Loutdoorwadingpools
(one wading pool for each population) containing aged well water at
theRensselaerAquaticLaboratoryinTroy,NY.Allpopulationsbegan
hatchingbetweenApril14and 15,2022.Oncetheyhatched,wefed
the tadpoles rabbit chow ad libitum (Blue Seal Fresh Show Hutch
Deluxe).Weusedhatchlingtadpolesfromtheseeggmassesinatime-
to-deathexperimentfollowedbyagrowthanddevelopmentexperi-
ment.Atleast1 weekpriortoeachexperiment,webroughttadpoles
fromeachpopulationintothelabtoacclimate.Inthelab,theanimal-
rearingroomwasmaintainedat21°Cwithalight:darkcycleof15:9 h.
2.2  | Time- to- death experiment
To assess the relative levels of tolerance of each population to road
salt contamination, we conducted a time-to-death (T TD) experi-
mentwhereweexposedtadpolestocontrolwater(19 mgCl/L) and
alethalconcentrationof8 g/Lof NaCl.Time-to-deathexperiments
intentionally use high concentrations of a pollutant (often higher
than experienced in nature) to determine whether different groups
in individuals (e.g., populations) differ in their relative tolerance over
ashor ttimeperiod(1–4 days),duringwhichtheanimalsarenotfed
(Brady, 2013; Bridges & Semlitsch, 2000; Semlitsch et al., 2000).
OnceTTDexperimentsfinddifferencesintolerancebasedonshort-
term times to death, researchers can examine environmentally rel-
evant concentrations over longer periods of time to determine if
differences in tolerance affect performance.
For this experiment, we used a fully randomized design that in-
volved the nine populations of wood frogs and the two salt treat-
ments. We placed one tadpole into each of the experimental units,
whichwere59 mLclearplasticcupsfilledwithapproximately45 mL
ofwater.Thelethalsaltdosewascreatedbyaddinglab-gradeNaCl
toaged tapwatertoreach aconcentrationof8 g/L NaCl,basedon
the concentration used by Buss et al. (2021). From each population,
we placed 15 individuals intocups containing water with a lethal
salt concentration and five individuals into cups containing control
water. Thus, there was a total of 180 cups in a completely random-
ized design. The control water was t ap water that we aged at least
24 hto allow any chlorinetoof f-gas.Wealsosetasidetenindivid-
uals from each population to estimate the initial average mass and
developmental stage (Gosner, 196 0) of each population. The initial
individualmasses of the populationsranged from33to 64 mg; de-
velopmental stages ranged from approximately 26 to 27 (Table 1).
Westarted the experiment on 26April and team memberstook
turns initially checking the tadp oles every 4 h for mor tality. Once
mortalitybegan,wecheckedtheexperimentevery2 handrecorded
the number of dead tadpoles from each population. We checked
for deaths by gently blowing water at the tadpoles using a pipette.
Nonresponsive tadpoles were considered dead. If it was unclear
whether a tadpole was still alive, we looked for a heartbeat under a
dissecting microscope. We set aside individuals who were declared
dead and double checked them at the subsequent check time. If we
determined that the tadpoles were still alive, we returned them to
theexperimentalarray.Checkscontinuedforatotalof96 h(30April).
Therewasnomortalityinthesalt-freecontrols.Uponcompletionof
theexperiment,weeuthanizedallindividualsusing2%MS-222.
FIGURE 1 Chlorideconcentrationsateachoftheninesitesatthetimeofwoodfrogeggcollection.Sitesarerepresentedbyunique
three-orfour-lettercodes.
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Weused pair wise log-ranktestswitha Bonferroni correction
to look for di fferences in t he Kaplan–Meier sur vival cur ves for
each population. While this analysis tests for differences among
the nine populations, it does not show what may be driving dif-
ferences in survival. Thus, our analysis sought to determine the
direct effect of the chloride concentration of the source pond
and the death rates of each individual. To do so, we conducted a
Cox mixed effects model. Our response variable in this model was
the probability of tadpole survival, regardless of the pond from
which they came. Our fixed ef fect s were the source-pond chlo-
ride concentrations, the mean individual mass of tadpoles in each
population, and their interaction. We included population as a ran-
dom effect in the model to control for other differences among
populations, aside from chloride concentration, that we did not
measure. We calculated hazard ratios for the fixed ef fect s using
the model parameter estimates. To do this, we raised the natural
root to the power of the parameter values. Subtrac ting the hazard
ratio from one gives the percent increase in survival that a param-
eter contributes to the overall survival of individuals in the study.
Parameter significance was determined using Wald Chi-square
analyses.AllanalyseswereconductedinRversion4.1.0usingthe
survival (Therneau, 2021), Survminer (Kassambara, 2021), coxme
(Therneau, 2020), and car packages (Fox & Weisberg, 2019).
2.3  | Growth and development experiment
To determine whether evolved salt tolerance came with any growth
ordevelopmentaltradeoffs,weconductedafollow-up experiment
on additional wood frog tadpoles from the same nine populations.
We used a randomized block design for this experiment with three
spatial blocks, where each block was a different shelf height in the
lab. In each block, experimental units were assigned one of the nine
populations and one of two salt treatments (control water with no
salt added vs. a higher sublethal salt concentration). We replicated
the 18 treatment combinations twice within each block, which pro-
vided six replicates across the entire experiment. Thus, there were 36
experimental units per block and a total of 108 experimental units.
Theexperimentalunitswere5-Lwhiteplastictubscontaining4 L
of aged tap water. On 9 May, we placed six tadpoles into each tub.
AswiththeTTDexperiment,wesetasidetenindividualsfromeach
population at the outset of the experiment to quantify the average
developmental stage (Gosner, 196 0) and mass of the individuals
used in the experiment from each population. These initial masses
ranged fr om 62 to 179 mg with developm ent stages r anging from
approximately25to28(Gosner,1960 ; Table 1).
Weagedalltapwaterforatleast24 htoallowchlorinetooff-gas.
Forthe sublethal salttreatment, we addedlab-grade NaCl in aged
tapwater toreach achlorideconcentration of165.5 ± 0.3 mg Cl/L
(mean ± SE).Thisvalue representsthemid-rangeofchloride values
in the ponds from which we collected the wood frogs (Figure 1). The
tap water in the no-salt treatment had a background chloride con-
centrationof25.9 ± 0.3 mgCl/L(mean ± SE).
We fed the tadpoles a ration of Tetra goldfish food (Spectrum
Pet Brands LLC) mixed with water ad libitum (starting at approxi-
mately 16.5 m g per tadpo le per day and in creasing up to ap proxi-
mately 22.2 mgpertadpoleperdayasthetadpolesgrew)overthe
course of the experiment. We conducted water changes approxi-
mately every4 days over thecourse of the experiment whenever
the water appeared murky.
Nine days into the experiment, we quantified tadpole activity
using scan sampling. Two observers made 10 observations each of
every tub over thecourse of 75 min, which produced 20 observa-
tions of each tub. The observers slowly walked by the t anks and
peered in so as not to disturb the t adpoles. For each tub, we re-
corded the number of individuals moving at a given moment. We
conducted the observations prior to feeding, given that satiated
tadpoles substantially reduce their activity to low levels. We used
the mean percentage of individuals moving in each tub as our re-
sponse variable. For the two tubs that had a tadpole not survive, we
adjusted the percent activity to reflect the reduced number of tad-
poles in that tub. Sur vival across the entire experiment was 99.7%.
Theexperimentwasterminatedafter22 days(31May),whenthe
tadpoles approached metamorphosis (i.e., Gosner stage 39). We then
determined the mass and Gosner stage of each tadpole and used the
mean values of each experimental unit as our response variables.
We used a linear mixed effects model to look for differences in
the relative growth rate of the tadpoles from the nine different pop-
ulations exposed to t wo salt treatments. Relative growth rate was
calculated as the difference in the natural log of final individual mass
and initial population mean mass, divided by the duration of the ex-
periment(i.e.,22 days).Ourmodelusedchlorideconcentrationsofthe
source ponds, salt treatment (salt or no salt), and the interaction be-
tween these variables as the fixed effects. We had a series of nested
random effects in this model, including block, population, and tub,
nested in that order. These random effects were in place to account
TAB LE 1  Themean(±SE) initial mass and median Gosner
developmental stage of wood frog tadpoles from each population
wereusedinthetime-to-death(TTD)andgrowth-rate
experiments.
Population
TTD experiment Growth experiment
Mass
(mg)
Gosner
stage Mass (mg)
Gosner
stage
HST 46 ± 3 26 143 ± 8 28
ATL 52 ± 4 27 116 ± 8 27
ALG 60 ± 3 26 101 ± 9 27
DCH 56 ± 2 26 128 ± 9 28
BOB 33 ± 2 26 124 ± 7 27
DBY 45 ± 4 26 112 ± 5 27
EGTP 64 ± 2 27 125 ± 7 27
COL 48 ± 2 26 140 ± 6 28
APHS 43 ± 3 26 120 ± 4 27
Note: Site abbreviations are the same as in Figure 1.
   
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for additional variation introduced by the blocks, the individual tubs,
and other aspect s of the natal ponds that we did not measure directly.
We looked at the changes in tadpole development using a mixed
effec ts model almost identic al to the one we used for relative grow th
rate. In this instance, the response variable was the change in the
Gosner stage for each individual tadpole. We calculated the change
in the Gosner stage by subtracting the average initial Gosner stage
of a given population from the final, measured Gosner stage of each
individual in the experiment. Our fixed and random ef fects for this
model were identical to the model examining relative growth rate.
Finally, we used a binomial mixed effects model to look for
differences in ac tivit y among the nine populations in the two salt
treatments. In this analysis, our response variable was whether an
individual was moving or not during each of the twent y obser va-
tion periods, hence the binomial model. The fixed and random ef-
fects variables in this model were the same as in the growth and
development analyses. For each of these analyses (relative growth
rate, development, activity), we used Wald II Chi square analyses
to determine the significance of the fixed effects (chloride concen-
tration, salt treatment, or their interaction). We conducted all our
analyses in R version 4.1.0 (R Core Team 2022) using the lme4 (Bates
et al., 2015) and car (Fox & Weisberg, 2 019) packages.
3  |RESULTS
3.1  | TTD experiment
ThewoodfrogsfromtheAPHSpopulationssurvivedabouttwiceas
longinthe lethal-salttreatment comparedtotheothereightpopu-
lations (Figure 2).Indeed,ourlog-ranktest showedthatthis group
was statistically different from all the others (all pairwise p values for
APHS < 0.01).TheAPHSpopulationalsohadthehighestconcentra-
tion of chloride at the time of egg collection (Figure 1). The survival
curves for the other eight the populations did not differ from each
other (all pairwise pvalues > .2). OurCoxmixed effects model, de-
signed to determine the explicit link bet ween chloride concentration
and survival, showed that chloride concentration had a significant,
negative effect on the probabilit y of dying in the TTD experiment
(Table 2). In other words, individuals collected from ponds with
higher chloride concentrations were more likely to survive than in-
dividuals collected from ponds with lower concentrations. However,
this effect was quite weak, with a Hazard Ratio of more than 0.99
meaning that for wood frogs in our study, a single unit increase in
chloride concentration confers less than a 1% increase in likelihood
of survival Indeed, it is likely that this weak but st atistically signifi-
cantrelationshipisdrivenentirelybytheAPHSpopulation.
3.2  | Growth and development experiment
While there were differences in the relative grow th rates of the tad-
poles (Table 3, Figure 3a), these dif ferences were not explained by
the chloride concentration of their natal pond, the salt treatments,
or their interaction. Indeed, none of our model terms were signifi-
cant and all effec t sizes were small.
Similarly, while there were some differences in development
among the nine populations (Table 3, Figure 3b), there were no sig-
nificant effec ts on development for any of the variables we included
in our models.
Tadpole activity was not affected by population, but was af-
fected by the salt treatment (Table 3, Figure 3c). Across all po pu-
lations, the moderate salt concentration made tadpoles less active.
There was no interac tion between population and salt treatment.
FIGURE 2 Thepropor tionofwoodfrogsalivefromeachoftheninepopulationsusedinthetime-to-deathexperimentwhenexposed
to8 g/LofNaCl.Warmercolorsindicatepopulationswhosesourcepondhadhigherchlorideconcentrationsandcoolercolorsindicate
populationswhosesourcepondhadlowerchlorideconcentrations.Theasteriskindic atessignificantlydifferentKaplan–Meyersurvivalas
calculatedusinglog-ranktest s(seetex t).Therewerenodeathsintheno-saltcontrols,sothesurvivalcurvesfortheninecontrolsarenot
shown.
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4  |DISCUSSION
The tolerance, grow th, development, and behavior of the wood frog
tadpoles in our experiments were largely consistent between each
of the nine populations with one notable exception. The popula-
tionfromthepond with the highestchlorideconcentration(APHS)
showed a muc h higher toleranc e to de-icing s alts than the oth er
eight, as demonstrated by its higher survival in the lethal salt dose
experiment. This finding suppor ts our hypothesis that wood frogs
from wetlands with higher salt concentrations can evolve higher salt
tolerance.
Prior to this study, there was mixed evidence about the evo-
lutiona ry responses of w ood frogs to de-icing sal ts. Our findin gs
agree with Brady et al. (20 19), who found that wood frog popula-
tions from Vermont exhibited superior locomotor performance
and fitn ess-re lated trait s (e.g., body m ass, fecund ity) if they c ame
from roadside ponds compared to populations from ponds far from
roads. That study found no differences in sur vival between roadside
versus woodland populations. However, it contrasted with studies
of wood frog populations from Connecticut that have shown that
de-icingsaltscanleadtomaladaptation(Brady,2013, 2017). When
studies have investigated the ability for wood frogs to adapt to
roadside habitat s with de-icing salt pollution, they havecompared
roadsidepopulationstothosefarfromroadsthatreceivenode-icing
salt pollution. Other work has shown that proximity to roads better
explains egg density than salinit y (Karraker et al., 2008) suggesting
that for some maladapted traits, aspects of being near a road other
than salinity may be important for determining the fitness of popu-
lations of wood frogs in these habitats. This could potentially explain
why nearly all our populations showed identical responses in their
growth and activity levels. That is, the evolved responses of wood
frogs to de -icing sa lts may also be af fected by fa ctors associ ated
with roadside ponds.
One potential explanation for the pattern in our data is that the
APHS population was only recently established and therefore had
not evolved maladaptation the ways that the other eight popula-
tions had. In some populations of wood frogs, individuals from ponds
far from roads have higher survival in high salt environments than
those from roadside ponds (Brady, 2013, 2017; Brady et al., 2022;
Forgione & Brady, 2022; Hall et al., 2017 ). However, it remains un-
certain how many generations it takes for maladaptation to develop
in wood frog populations living adjacent to roads. Rapid evolution,
including adaptation and maladaptation, still requires multiple gen-
erations for trait change to occur (Hendr y, 2017 ). However, this ex-
planation would assume that maladaptation is the norm across all
populations which isn't the case (Brady et al., 2 019).
An alternative explanation is that the APHS population has
evolvedhighertolerancetode-icingsaltsduetothehigherconcen-
tration of salt in their source pond. Whether the increased toler-
ance we observed is the product of true evolution or phenot ypic
plasticity (e.g., Hua et al., 2015) is an open question. Regardless, the
fact that we only saw increased tolerance in the population coming
from the pond with the highest chloride concentration would sug-
gest that there may be some threshold level of chloride pollution
necessary for wood frogs to respond. Our highest salt concentration
(774 mgCl/L) is similar to the highest concentrations obser ved in
other studies, yet several of those studies did not detect increased
tolerance in the highest salt populations (Brady & Goedert , 2017;
Brady et al., 2017). However, as noted earlier, a subsequent study in
Vermontdiddetectsuperiorfitness-relatedtraitsinroadsidepopu-
lations living with elevated salt concentrations (Brady et al., 2019).
Alternatively, the higher chloride tolerance of the APHS pop-
ulation could be the result of phenotypic plasticity. While all the
TAB LE 2  TheresultsofaCoxmixed-effec tsmodelexaminingchlorideconcentrationofthesourceponds,tadpolemass,andtheir
interactionontadpolesurvivalinthetime-to-deathexperiment.
Parameter Estimate Variation HR d.f.
X2
p
Pond chloride −9.9 3× 10 −3 5.97 × 10−3 0.990 18. 41 .004
Mass −1. 94  × 10−2 2.84 ×10−2 0.028 10.04 .834
Chloride × Mass 1.62 × 10 −4 1.27 × 10−4 0.00 01 11.65 .199
Population (random effect) 0.2 59 0. 51
Note: The p opulation was included in the model as a random effect. The estimate column shows the calculated parameter values for the fixed effects
and the amount of variation explained by the random effect. The variation column shows the standard errors for the fixed effe cts and the st andard
deviation for the random ef fect of the population. HR is the hazard ratio, calculated by t aking the exponent of the coefficient. Degrees of freedom,
X2
values, and p values were calculated using a Type II Wald
X2
analysis.
TABLE 3 ANOVAresult sofwoodfrogpopulationandsalt
treatment on the relative growth rate, Gosner developmental stage,
and activity of t adpoles.
Response variable
Explanatory
variable d.f. F p
Relative growth
rate
Population (P) 833.65 <.0 01
Salt (S) 1 1.49 .225
P × S 81.33 .238
Gosner
developmental
stage
Population (P) 81.95 .62
Salt (S) 1 0.01 .919
P × S 80.214 .988
Activity Population (P) 81.06 .40
Salt (S) 1 5.00 .03
P × S 80.74 .66
   
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tadpoles from each population in our experiments underwent the
same exposure to road salts, plastic responses can still be present in
the form of inherited environmental ef fect s, such as maternal effects
(Rossiter, 1996).Aswithfrequencydependentselection,ourexper-
iment was not designed to test for mechanisms such as maternal
effects. However, in the future, combining laboratory and field ex-
periments would be helpful for exploring this possibility further.
Source pond chloride concentrations and our experimental salt
treatments had no effec t on the growth or development of the wood
frog tadpoles. However, the experimental salt treatment did depress
FIGURE 3 The(a)relativegrowthrate,(b)changeinGosnerstage,and(c)activityoftadpolesfortheninewoodfrogpopulationsin
the presence and absence of a sublethal salt concentration. The populations are plotted in reference to the chloride concentration of their
source ponds. Data points represent means ±1 SE.
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activity levels regardless of source pond chloride levels. The reduced
activity levels in response to experimental salt treatment s align with
other studies that have found similar results in wood frogs (Hall
et al., 20 17) and other amphibians (Squires et al., 2010), although
such affects can change over ontogeny (Kearney et al., 2014). This
finding further reinforces the idea that current salt exposure may
be more important for determining behavioral responses than the
historic saltiness of the natal pond.
Interestingly,thehigher tolerance tode-icingsaltsin the APHS
population did not lead to differences in growth rate, development,
or activity. This is surprising, as there are good reasons to believe
thatthesetraitsshouldbeeitherhigherorlowerintheAPHSpopu-
lation compared to the others. For example, it would make sense that
havingahighertolerancetode-icingsaltswouldcoincidewithfaster
growth rates and higher activity levels, as shown in other studies
(Hall et al., 2017 ).Alternatively,itwouldnothavebeensurprisingto
see a tradeoff in growth and development rates with increased envi-
ronmental stress (Berven et al., 1979). Indeed, tradeoffs associated
with tolerance to pollutants have been recorded in wood frogs in
other contexts (Hua et al., 2017). However, the growth and activit y
levels of the populations were not explained by the concentration of
chloride in their natal ponds. It's possible that tradeoffs exist along
other trait axes that we did not measure, such as parasite resistance,
which has been shown to decrease with increasing chloride concen-
trations (Milotic et al., 2017). However, given the myriad of ways that
maladaptationtode-icingsaltshasbeenrecordedinwoodfrogs,we
must be careful to design studies that accurately assess whether
trait changes are the result of tradeof fs or direct selection pressures
(Schluter et al., 1991).
Unfortunately, we do not have historic al records of the chloride
concentrations in any of the ponds we used in our experiment, but
it seems likely that similar concentrations have been occurring for
decades.Whiletheconstituentsodiumandchlorideionsofde-icing
salts are typically conserved in waterbodies (Dugan et al., 2017;
Godwin et al., 2003), t hey can fluct uate, especia lly since de-icing
salt application is not always consistent due to variation in weather
patterns (Venäläinen, 2001). While we collected wood frogs from
ponds that had a gradient in chloride concentrations at the time of
collection, it is possible that these concentrations could experience
springtime variation over multiple years.
That the population of wood frogs from the pond with the
highest de-icing salt pollution showed the highest tolerance
was encouraging from a conservation perspective. However,
it is impor tant that we exercise caution when extrapolating
short-term, high-concentration salt exposures to longer-term,
lower-concentrationexperiments innature,becausesometimes
one can observed contradictor y outcomes, as observed in lar-
val Ambystoma salamander populations (Brady, 2012; Brady
et al., 2017). Moving forward, it will be necessary to begin fo-
cusing research effort s on populations of wood frogs from ponds
with very high levels of chloride contamination (i.e., greater than
700 mg/L).Indeed, our mostcontaminated pond had a chloride
level of 774 mg/L whichishigher thanmany of the ponds used
in previous studies (Brady, 2013, 2017). Focusing on highly im-
pacted ponds will not only help determine whether our observa-
tion is par t of a broader pattern, but also provide insight into the
mechanisms that might drive higher tolerance to chloride among
wood frog populations.
4.1  | Conclusions
The results of this study demonstrate that populations of amphib-
ians, and perhaps many other taxa, have the abilit y to evolve in-
crease salt tolerance when exposed to high concentrations of salt
in ponds and wetlands. Thus, we may need to focus our research
efforts on populations of from ponds with ver y high levels of chlo-
ridecontamination(i.e.,greater than 700 mg/L).Ifsuchevolution
of increased salt tolerance is common in aquatic taxa, it sug gests
that entire communities may have the ability to evolve higher
tolerance, which would allow these species to persist while we
work to reduce freshwater salinization, particularly through more
targeted applications of road salts that can reduce salt use by as
muchas50percent(Hint zetal.,2022). Future studies should ex-
amine many other populations of amphibians and associated taxa
and also examine whether the tolerance to salinization is constitu-
tive or if it can be rapidly induced, as has been observed in many
pesticides (e.g., Hua et al., 2015).
AUTHOR CONTRIBUTIONS
Rick Relyea: Conceptualization (equal); data curation (equal); formal
analysis (equal); funding acquisition (equal); investigation (equal);
projec t administrat ion (equal); super vision (equal) ; writing – origi-
naldraft(equal);writing–reviewandediting(equal).Brian Mattes:
Investigation (supporting). Candace Schermerhorn: Investigation
(supporting). Iasaac Shepard: Conceptualization (equal); formal anal-
ysis (equal); investigation (lead); methodolog y (equal); supervision
(equal);writing–originaldraft(equal).
ACKNOWLEDGEMENTS
We thank Nate Fahey and McKenna Conners for their assistance
with the experiment. We also thank the editor and anonymous
reviewers for their helpful feedback. Major funding was provided
by NSF grant D EB 16-55168 to RAR a nd Rensselaer Poly technic
Instituteendowedchairfunds toRAR .Thisresearchwas approved
undertheuniversityIACUCprotocolREL0 01-22.
FUNDING INFORMATION
Major funding was provided by NSF grant DEB 16–55168 and
Rensselaer Polytechnic Institute endowed chair funds.
CONFLICT OF INTEREST STATEMENT
The authors declare no conflicts of interest .
DATA AVAIL AB ILI T Y STAT EME N T
Alldatawillbepubliclyarchiveduponpublicationacceptance.
   
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SUPPORTING INFORMATION
Additional supporting information can be found online in the
Suppor ting Information section at the end of this article.
How to cite this article: Relyea, R., Mattes, B., Schermerhorn,
C., & Shepard, I. (2024). Freshwater salinization and the
evolved tolerance of amphibians. Ecology and Evolution, 14,
e11069. https://doi.org/10.1002/ece3.11069
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Organisms that rely on aquatic habitats in roaded landscapes face a growing array of consequences from pollution, especially due to freshwater salinization. Critically, these consequences can vary from population to population depending on exposure histories and evolutionary responses. Prior studies using transplant and common garden experiments have found that aquatic-stage wood frogs (Rana sylvatica) from roadside populations are less fit in the wild and more sensitive to road salt than their counterparts from woodland populations away from roads. While this pattern is consistent with local maladaptation, unresolved insights into the timing and duration of these effects leave open the possibility that negative outcomes are countered during development. Here, we asked whether the survival disadvantage of roadside wood frogs is stage specific, and whether this disadvantage reverses before metamorphosis. We used a common garden road salt exposure experiment and a field-based reciprocal transplant experiment to examine differences in survival across life-history stage and with respect to population type. In each experimental context, roadside embryos showed a survival disadvantage relative to woodland embryos, and this disadvantage was not reversed prior to metamorphosis. We also found that salt exposure delayed metamorphosis more strongly for roadside than woodland populations. Together, these results suggest that local maladaptation in aquatic-stage wood frogs is driven by embryonic sensitivity to salt and that roadside populations are further compromised by delayed developmental rates. Future studies should consider which embryonic traits fail to adapt to salt toxicity, and how those traits might correlate with terrestrial trait variation.
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• There is increasing evidence that populations of non‐target wildlife species can evolve tolerance to pesticides. As ecosystems become increasingly exposed to chemical contaminants globally, it is important to consider not only the immediate consequences of contaminant exposure but also the potential costs associated with evolved responses. Theory predicts there may be trade‐offs, including increased susceptibility to parasites, associated with evolved pesticide tolerance. It remains unclear, however, how environmental context (i.e. presence/absence of pesticides in the contemporary environment) interacts with evolved pesticide tolerance levels to influence infection outcomes. • Several studies have demonstrated that wood frog (Rana sylvatica) populations close to agriculture, where frequent exposure to pesticides is more likely, show higher baseline tolerance to pesticides than do populations far from agriculture. Using eight wood frog populations from across an agricultural gradient, we explored patterns of variation in susceptibility to parasites associated with a population's proximity to agriculture (a proxy for pesticide tolerance), and how these patterns are influenced by experimental exposure of tadpoles to the insecticide carbaryl. We did this by first placing tadpoles in an environment containing the pesticide carbaryl (1 mg/L) or in a pesticide‐free control environment for 5 days, and subsequently exposing tadpoles to trematodes (Echinostoma trivolvis) or ranavirus (frog virus 3). • We found that variation in trematode susceptibility was related to the tadpole populations’ proximity to agriculture. Individuals from populations located close to agriculture were modestly more susceptible to trematode infections than individuals from populations farther from agriculture. Ranavirus susceptibility was not associated with proximity to agriculture. • Surprisingly, exposure to carbaryl increased the survival rates of tadpoles infected with ranavirus. There were no other significant effects of carbaryl exposure on the measured disease outcomes. • This study provides evidence for a potential trade‐off between trematode resistance and putative pesticide tolerance. We show that host populations can vary significantly in their susceptibility to pathogens, but that pesticide exposure does not always increase parasite susceptibility or uniformly exacerbate disease outcomes. Further research is needed to determine how genetic variation among populations impact susceptibility to parasites, and if these patterns of susceptibility are consistent across space and time.
Article
Understanding how environmental factors and short-term evolution affect the growth of invasive plants is a central issue in Invasion Biology. For macrophytes, salinity is one of the main factors determining distribution along estuarine environments. Urochola arrecta is a Poaceae with high invasive potential in several freshwater and estuarine ecosystems. In South Brazilian estuaries, this species is found sparsely in mangroves, and invades successfully freshwaters and areas with low salinity. We experimentally described the U. arrecta tolerance to salt. Furthermore, we tested if the response to the saline gradient depends on the population origin, through an experiment with populations inhabiting estuarine and freshwater ecosystems. We designed the experiment with three populations of this species, expecting that estuarine populations were more resistant to salinity. Plants grew in a salinity gradient and after 40 days we measured macrophytes biomass and length. Salinity was highly stressful for U. arrecta independently of its origin. Even so, plant growth differed significantly among populations. Despite higher growth, the population originated from freshwater habitats presented the fastest decrease in performance indicators with increasing salinity. This result indicates short-term evolutionary changes because all populations grew common-garden conditions in our experiment. Furthermore, salinity did not prevent the full establishment of this plant, since almost all propagules developed roots even in the saline treatments. Differences among populations suggest that invasion potential of this species can be higher than predicted by the environmental conditions of current invaded sites. Constant monitoring in estuarine invaded ecosystems is central to manage invasions in critical ecosystems, such as mangroves areas.