Discussion
Longer-term (ca . 5 year) invasion by P. megacephalareduced carbon fixation in A. drepanolobium by 69% during the
growing (wet) season, consistent with other studies demonstrating that
invasive species can alter fundamental ecosystem processes (a review of
ecosystem functions affected by invasions: Hooper et al. 2005;
invasive insects reducing hardwood forest productivity: Kurz et
al. 2008; Albani et al. 2010; Clark et al. 2010;
disruption of pollination by invasive insects: Morales et al.2017). The combination of shorter-term small or neutral effects of
recent invasion on leaf-level photosynthesis with longer-term large
reductions in canopy photosynthesis for trees that had been invaded for
5 years highlight that some ecologically relevant effects of invasive
species can lag behind their initial appearance in a habitat (Crooks
2005; Strayer et al. 2006; Simberloff 2011). Finally, the large
positive effect of vertebrate herbivore exclusion on canopy
photosynthesis in invaded habitats demonstrates how invasive insects can
indirectly interact with native fauna, including vertebrates, to
substantially change carbon fixation for foundational plants.
Our results from Transition sites suggest that P. megacephalatriggers minimal (if any) benefits for newly invaded trees, thus
indicating that the loss of native ant mutualists has little direct
effect on leaf-level photosynthesis in the short term. Wet season
leaf-level photosynthesis and transpiration were nearly identical
immediately before and after invasion for Transition trees, while the
significant decline for both variables over the same period for Control
trees may simply be driven by a decline in water availability for
Control trees between the 2017 and 2018 wet seasons. Recently invaded
trees experienced declines in dry-season leaf-level photosynthesis that
were almost twice as large as declines for Control trees, perhaps
because mixed feeders that forage on woody species during the dry season
(Illius & O’Connor 1999) began to target their large and unprotected
leafy canopies. The recent extirpation of C. mimosae by P.
megacephala does not appear to cause increases in leaf-level
photosynthesis, addressing our first research question about how the
recent removal of native ant mutualists affects leaf photosynthetic
rate. Crematogaster mimosae imposes a low net cost for the
host tree compared to other ant species like C. nigriceps andC. sjostedti (Stanton & Palmer 2011), which may explain why
their extirpation has no immediate effect on leaf physiology. Instead,
our BACI experiment suggests that recently invaded trees become targets
of herbivory during dry seasons, which may rapidly reduce leaf-level
photosynthesis.
The longer-term effects of P. megacephala invasion on wet season
carbon fixation is likely to affect how surviving invaded A.
drepanolobium produce biomass and interact with other savanna species.
In savannas that have been invaded for > 5 years, a
2-meter-tall tree has a canopy photosynthetic capacity of onlyca . 31% of the carbon fixation per hour as a comparable
uninvaded tree during the wet season, the primary growing period for
many African acacias (Gourlay 1995). While ca . 20% of
longer-term invaded trees at OPC experience complete destruction by
large herbivores, ca . 60% experience mild to moderate levels of
canopy damage (Riginos et al . 2015): our findings apply to this
large majority of trees that survive for years after invasion. Reduced
canopy-level photosynthesis can limit the availability of dissolved
sucrose in aboveground tissue for A. drepanolobium (P. Milligan,
unpublished manuscript), which is an important plant resource for growth
(e.g., Wiley & Helliker 2012) and response to biotic and abiotic stress
(e.g., Hummel et al. 2010; Engelsdorf et al. 2013). Low
carbon availability can reduce population growth (McDowell 2011; Wiley
& Helliker 2012), and likely contributes to A. drepanolobiumpopulation declines in longer-term invaded areas predicted by
empirically derived demographic models of OPC trees (B. Hays,
unpublished manuscript). Carbon limitation can prevent trees from
producing aboveground biomass (Allen et al. 2010; McDowell 2011),
which would reduce the influence of A. drepanolobium on non-woody
plant growth in its understory (Riginos et al. 2009) and on the
visibility of predators and prey in black cotton savannas dominated byA. drepanolobium (Riginos 2015). Also, carbon limited trees
likely have fewer carbohydrates to support endosymbionts, which could
affect nitrogen-fixing bacteria in A. drepanolobium roots that
input N into black cotton soil (Fox-Dobbs et al. 2010).
The interactive effect of invasion and vertebrate herbivory is likely
the primary driver of leaf- and canopy-level photosynthesis and
transpiration decline for longer-term invaded trees. The displacement of
aggressive native C. mimosae by P. megacephala results in
more intense browsing of A. drepanolobium by elephants (Riginoset al. 2015), which suppresses canopy size for A.
drepanolobium and for other savanna trees (Pellew 1983; Biggs & Jacobs
2002; Goheen & Palmer 2010), and thus reduces canopy-level
photosynthesis. At the leaf-level, P. megacephala may function
similarly to the native C. sjostedti , which provides negligible
defense (Martins 2010) and is associated with low leaf-level
photosynthesis when large herbivores are present (King & Caylor 2010).
directly result from damage by herbivores (e.g., Delaney et al.2008) or indirectly result from the tree’s production of antiherbivory
compounds in leaves as a response to damage (in this system: Ward &
Young 2002; across plants: Ishida et al. 2008; Sumbele et
al. 2012; Keenan & Niinemets 2016, see Note S5). While we did not
observe reductions in leaf- or canopy-level photosynthesis on C.
mimosae -removal trees in uninvaded areas, those trees may have
benefitted from “associational defense” (Barbosa et al. 2009)
with neighboring trees that were occupied by defensive native ants (see
Note S5).
Compared to vertebrate herbivores, invasive P. megacephala had
smaller but significant direct negative effects on A.
drepanolobium carbon fixation. This may be driven by P.
megacephala ’s habit of nesting around tree roots (P. Milligan, pers.
observation), which can have large negative impacts on carbon fixation
and leafy growth for A. drepanolobium saplings (Milligan et
al . unpublished manuscript). Pheidole megacephala may also
affect tree physiology through facultative interactions with other
insect pests in the canopy, which were present in both ant-present and
ant-excluded tree canopies >8 months after canopies were
initially fogged with insecticide (P. Milligan, pers. observation).
While we did not explicitly examine these relationships here, P.
megacephala tends lycaenid caterpillars (pers. observation T. Palmer; a
widespread association in Australia, Eastwood & Fraser 1999) and
tolerates phloem-feeding cerambycid larvae (pers. observation P.
Milligan) in the canopy. Infestations of phloem-feeding insects can
affect the photosynthetic rates and water use efficiency of many plant
species (Cockfield et al. 1987; Meyer & Whitlow 1992; Haaviket al. 2008; Golan et al. 2015), which may further limit
tree above- and belowground productivity (Wiley & Helliker 2012).
While our finding of strong interactive effects of an invasive ant and
vertebrate herbivores on carbon fixation of a dominant plant is novel,
there are some parallels to be found with other systems. Herbivores are
often more selective for high quality forage, such as the highly
nutritious leaves produced by A. drepanolobium (Rubanza et
al. 2007), in other savanna systems (e.g., Roques et al. 2001;
Kos et al. 2012; Abraham et al. 2019). Thus, plants likeA. drepanolobium with highly nutritious leaves may experience
large changes in herbivore pressure if their deterrents against
herbivory are disrupted by invasive insects. Chronic herbivory often
imposes cumulative aboveground growth costs for plants in other systems
(e.g., Kozlov & Zvereva 2017; Wilson et al. 2018), and those
increased metabolic costs can negatively affect leaf- and canopy-level
photosynthesis (Wiley & Helliker 2012). McDowell (2011) reviewed how
invasive insects contribute to carbon limitation and tree mortality
during periods of environmental stress, but it is unknown whether
interactive effects between invasive insects and native herbivores may
be a more general phenomenon in terrestrial ecosystems.
The longer-term loss of photosynthetic capacity for ant-plants in
invaded habitat reduces A. drepanolobium ’s carbohydrate pool,
which may affect other ecosystem processes to which this foundational
tree contributes. For example, A. drepanolobium imports nitrogen
into N-limited black cotton vertisols via N-fixing root endosymbionts
(Fox-Dobbs et al. 2010). If host plants reduce resource
allocation to roots in invaded habitats, this could in turn reduce both
N-fixing symbiont activity and soil respiration (seen in a large-scale
girdling experiment in boreal forests, Högberg et al. 2001).
Potentially compounding this effect, elephants may reduce tree cover
within invaded savannas over the longer term, further reducing N inputs
into the system, as has been shown in other areas of East Africa where
removal of acacia species reduces both the total content and
mineralization of C and N in soils (Glaser et al. 2001). Finally,Acacia drepanolobium has density-dependent effects on the
productivity of understory plants (Riginos et al. 2009), and thus
the resource availability and productivity of invaded trees may also be
linked to understory productivity. By increasing the mortality (Riginoset al. 2015) and decreasing the carbon fixation of this
monodominant tree species, P. megacephala invasion may
fundamentally alter carbon cycling and connected ecosystem processes in
these savannas.
Acknowledgements: We thank the Kenyan government
(NACOSTI/P/18/4376/9459) for their permission to conduct this work.
Gabriella Mizell, Nelly Maiyo, Jackson Ekadeli, Gilbert Buseinei, Isaac
Kipkoech, and John Mosiany provided excellent field assistance.
Elizabeth Pringle provided helpful comments during manuscript
preparation, and three anonymous reviewers provided valuable feedback.
Mpala Research Centre administration and the Ol Pejeta Conservancy
management team (particularly Samuel Mutisya and Benard Gituku) provided
substantial logistical support. This research was supported by a
University of Florida International Center RADS grant to PDM, a
Smithsonian ForestGeo grant to PDM, a National Geographic Society Young
Explorer grant to PDM, and a National Science Foundation grant (NSF DEB
1556905) to TMP, CR and JRG.