Research
http://dx.doi.org/10.1098/rspb.2013.3280
ecology, palaeontology
trophic organization
†Present address: Quid, 733 Front Street,
Highly resolved early Eocene food webs
show development of modern trophic
action data for 700 taxa from the 48 million-year-old latest early Eocene Messel
Shale, which contains a species assemblage that developed after an interval ofSan Francisco, CA 94111, USA.
Electronic supplementary material is available
at http://dx.doi.org/10.1098/rspb.2013.3280 or
via http://rspb.royalsocietypublishing.org.Author for correspondence:
Jennifer A. Dunne
e-mail: jdunne@santafe.eduKeywords:
food webs, Messel Shale, early Eocene,
network structure, niche model,Received: 16 December 2013
Accepted: 18 February 2014
Subject Areas:Cite this article: Dunne JA, Labandeira CC,
Williams RJ. 2014 Highly resolved early Eocene
food webs show development of modern
trophic structure after the end-Cretaceous
extinction. Proc. R. Soc. B 281: 20133280.rspb.royalsocietypublishing.orgprotracted environmental and biotal change during and following the end-
Cretaceous extinction. We compared the network structure of Messel lake and
forest foodwebs to extantwebsusinganalyses that account for scaledependence
of structure with diversity and complexity. The Messel lake web, with 94 taxa,
displays unambiguous similarities in structure to extant webs. While the
Messel forest web, with 630 taxa, displays differences compared to extant
webs, they appear to result from high diversity and resolution of insect–plant
interactions, rather than substantive differences in structure. The evidence pre-
sented here suggests that modern trophic organization developed along with
the modern Messel biota during an 18 Myr interval of dramatic post-extinction
change. Our study also has methodological implications, as the Messel forest
web analysis highlights limitations of current food web data and models.
1. Introduction
Comparative analyses of extant foodwebs have revealed generalities in the under-
lying network structure of trophic interactions (feeding relationships) among
co-occurring taxa regardless of habitat [1–5]. The question of whether such gener-
ality extends to ancient ecosystems remains open, as previous food web studies
of Late Cretaceous terrestrial assemblages [6], Permian and Triassic terrestrial
assemblages [7] and Cambrian marine assemblages [8] used low-resolution,
high-uncertainty data that were highly space and/or time-averaged. The
Cambrian study reported similarities in ancient and extant structure based on
webs with 50 or fewer taxa. The Late Cretaceous and Permian–Triassic studies
assumed similar structure to extant webs as a way to create instances of possible
palaeofoodwebs from aggregated, guild-level fossil data [6,7]. Here, we present
and analyse new food web data comprised of thousands of highly resolved,
spatially and temporally constrained feeding interactions among hundreds
of aquatic and terrestrial taxa representing probably the best preserved post
Cretaceous–Palaeogene (K–Pg) continental biota, the 48 Myr-old Messel deposit.
Profound environmental events and their biotal effects occurred in the 18 Myr
between the end-Cretaceous mass extinction and the deposition of the Messel
& 2014 The Authors. Published by the Royal Society under the terms of the Creative Commons Attribution
License http://creativecommons.org/licenses/by/3.0/, which permits unrestricted use, provided the original
author and source are credited.structure after the end-Cretaceous
extinction
Jennifer A. Dunne1,2, Conrad C. Labandeira3,4 and Richard J. Williams5,†
1Santa Fe Institute, 1399 Hyde Park Road, Santa Fe, NM 87501, USA
2Pacific Ecoinformatics and Computational Ecology Lab, Berkeley, CA 94703, USA
3Department of Paleobiology, National Museum of Natural History, Smithsonian Institution, Washington,
DC 20013-7012, USA
4Department of Entomology and Behavior, Ecology, Evolution and Systematics Program, University of Maryland,
College Park, MD 20742, USA
5Microsoft Research, Cambridge CB3 OFB, UK
Generalities of food web structure have been identified for extant ecosystems.
However, the trophic organization of ancient ecosystems is unresolved,
as prior studies of fossil webs have been limited by low-resolution, high-
uncertainty data.We compiled highly resolved,well-documented feeding inter-
of the models are also scale-dependent, generally showing sig-
certainty level when three or more categories provided evidence
for a link, or when gut contents were identified. The intermediate
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281:20133280
2assemblage. Evidence for ecologically unbalanced food webs
several million years into the Palaeocene aftermath of the
K–Pg boundary crisis [9] comes from exceptionally depaupe-
rate floras [10,11], plant–insect interaction data reflecting
severely unbalanced ecosystems [12], unstable mammalian
community structure [13], and reptile and bird gigantism
amid elevated greenhouse conditions that approached lethality
in some tropical regions [14,15]. A second, early Eocene series
of events was characterized by a sudden spike in significantly
elevated temperatures and pCO2 levels of the Palaeocene–
Eocene Thermal Maximum (PETM) [16,17] that induced new
types and high levels of insect herbivory [18]. Soon after this
105 year-long spike, major biogeographic and taxic transform-
ation of the biota ensued, such as major latitudinal shifts of
floras [19], penecontemporaneous diversification of termite
[20], ant [21] and bee [22] social insect clades, and replacement
of Palaeocene-type warm-blooded vertebrates by new major
lineages of Eocene birds [23] and mammals [13,24] that persist
to the present day.
These diversification events continued during a prolonged,
multi-million-year-long intensification of greenhouse condi-
tions at the Early Eocene Climatic Optimum (EECO), in
which temporally constrained pulses of elevated temperature
and pCO2 levels and various Eocene Thermal Maxima rivalled
that of the PETM [16]. During the EECO and immediately prior
to Messel deposition, another biotal transformation occurred
concomitant with a greenhouse-to-icehouse shift in the phys-
ical environment, signalled by climate cooling and freshwater
flooding of the Arctic Ocean. This shift was attributable to
major effects of oceanic heat transport reflected in the Azolla
Event [25]. These K–Pg to Messel events (electronic sup-
plementary material, table S5) likely affected food web
structure, particularly for Northern Hemisphere ecosystems,
that would represent a major, cumulative effect of the previous
18 Myr and not the subsequent 48 Myr of ecosystem change
reflected in modern ecosystem structure. As recently summar-
ized in a prominent review, which referenced the K–Pg crisis,
‘Mass extinction events may continue to affect the structure of
biotic interactions long after ecosystems have recovered to pre-
extinction diversity levels’ [26, p. 499]. These factors suggest
that it is an open question whether Messel food web organiz-
ation would be similar or anomalous in comparison to extant
web structure.
The Messel lacustrine deposit, near Darmstadt, in central
Germany, is of latest early Eocene age, based on radioisotopic
dates [27]. The maar lake strata is part of the Messel Formation
and consists of 190 m of oil shale in a 0.7 km2 basin [28] that rep-
resents from 1.0 to 1.6 Myr of time [29], with 0.6 Myrof this time
providing a sedimentologically and climatically circumscribed
record [30] (electronic supplementary material, methods S1).
The Messel biota records a considerably abbreviated geologic
window of deposition both temporally and spatially (electronic
supplementarymaterial, methods S2), increasing the likelihood
of ecological co-occurrence and interactions of preserved
species. Compared to 14 other well-documented and excep-
tionally preserved fossil deposits [31], Messel’s spatio-
temporal confinement lies within the top two or three,
exceeded by narrower spatial extent, temporal resolution or
both, only by the Cambrian Burgess Shale, Devonian Rhynie
Chert and Pleistocene Rancho La Brea asphaltum deposits.
Detailed species and feeding interaction data compiled
for the Messel system were used to create two habitat-specific
lake and forest food webs to ensure spatial co-occurrence andcertainty level was assigned when two categories applied and
the lowest certainty level corresponded to only one category of
evidence. By operationalizing the assignment of links with expli-
cit guidelines, assumptions used to establish the certainty of links
were kept to a minimum.
(b) Food webs
A lake web was extracted from the full Messel web by eliminating
links that involve solely terrestrial organisms. The remaining data
were purged of dangling animals that lack food chains connecting
them to at least one aquatic basal taxon, as well as any resource or
consumer links of those animals. A forest web was similarly gener-
ated, but instead eliminated links that involve entirely aquatic
organisms. Taxa that occur in both habitats at some point in their
life cycle can appear in either or both habitat-specific webs, as
long as they retain at least one food chain connecting them to a
basal taxon in that habitat. Reduced, higher certainty versions of
all threeMesselwebswere constructedbyeliminating low-certaintynificantly decreasing fit with increasing species richness or
simple measures of complexity [33,34,38–40]. This provides
an additional way to compare network structure of food
webs with very different numbers of species and links, as is
the case in this and a previous study [34].
2. Material and methods
(a) Species and trophic links
TheMessel dataset [41] includes all documented species deposited
within the small maar lake basin, including taxa from the lake’s
water column and benthos and from the immediately surrounding
paratropical forest [27,29,30]. The Messel deposit provides a
remarkably comprehensive record of taxa from all trophic levels
(electronic supplementary material, methods S3). Evidence used
to assign trophic links between Messel taxa came from 10 lines
of indirect to direct observations: (i) taxonomic uniformitarianism,
(ii) functional morphology, (iii) gut contents, (iv) damage patterns,
(v) stratigraphic co-occurrence, (vi) body size, (vii) coprolites,
(viii) host relationship, (xi) chemical and isotopic signatures and
(x) ichnological evidence (electronic supplementary material,
figures S1–S5) [41]. For each evidence category, one or more oper-
ational guidelines from ecology or palaeoecology were used to
infer a link between a consumer and a resource taxon. These 10 cat-
egories have been used informally throughout the modern and
fossil continental record for inferring trophic roles of organisms
[42–46]. More detailed description of the lines of evidence with
particular reference to the Messel ecosystem can be found in the
electronic supplementary material, methods S4.
The 10 lines of evidence were used to assign one of three cer-
tainty levels to each inferred link [41]. We assigned the highestpotential interaction among taxa within each food web. The
Messelwebswere compared to foodwebs from extant habitats,
in particular food webs that portray cumulative interactions
over time, using model-based analyses of several aspects of
network structure. Simple models like the niche model gener-
ate food web structure similar to that observed for empirical
webs [32,33]. Here, following the approach of a previous
study [34], we use the niche and othermodels as normalization
tools whose output provides ways to compare the structure of
food webs with variable numbers of species and links, given
the well-documented scale dependence of food web structure
on diversity and complexity of the web [2–4,34–37]. The fits
(electronic supplementary material, table S1). We excluded extant
; L, num
interm
rsions.)
C
0
0
0
0
0
0
0
0
0.059 28.0 30.5 41.5
0
0
0
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3food webs based on narrowly constrained temporal sampling
(e.g. webs based on gut contents sampled on one or a few days),
focusing on webs that represent cumulative, likely trophic
interactions among taxa that co-occur and have the possibility
of interacting, similar to the nature of the Messel lake and forest
food webs.
(c) Analyses
We analysed several commonly studied aspects of food web struc-
ture to provide a broad comparison of the trophic organization
ofMessel and extantwebs.We used a set of threemodelling frame-
works and associated analyses described in more detail elsewherelinks and purging the datasets of dangling animals and their links.
We generated ‘trophic species’ versions of eachweb by aggregating
taxa with the exact same set of predators and prey [47]. Following
convention [1–5,8,32–35], we focused analyses on trophic species
webs for the Messel lake and forest food webs and 30 extant habi-
tat-specific webs used in previous comparative structural studies
Table 1. Basic properties of the Messel Shale food webs. (S, number of taxa
Cert-Low, Cert-Int, Cert-High indicates the percentages of links that are low,
low-certainty links and associated taxa. ‘Tro.’ refers to trophic species web ve
web version S L L/S
full 700 6444 9.21
forest 630 5534 8.78
lake 94 517 5.50
full Red. 630 4602 7.30
forest Red. 557 3885 6.97
lake Red. 90 370 4.11
full Tro. 700 6444 9.21
forest Tro. 629 5530 8.79
lake Tro. 93 508 5.46
full Red. Tro. 630 4602 7.30
forest Red. Tro. 556 3881 6.98
lake Red. Tro. 88 360 4.09[34]. First, we tested the fit of cumulative resource (generality) and
consumer (vulnerability) distributions of each food web to predic-
tions of a null model based on maximum information entropy
(MaxEnt) [38]. We tested the fit of MaxEnt predictions (n ¼ 1000)
to empirical distributions by calculating goodness of fit, f G, and
relative width of the degree distribution, W95, specifically the
width of the resource distribution Res W95 and of the consumer
distribution Con W95. When f G  0.95, the empirical web’s
degree distribution does not differ significantly from the model
distribution at the 95% confidence interval. When 21  W95  1,
the empirical distribution is neither significantly narrower
(W95, 21) nor broader (W95. 1) than the distribution predicted
by the model at the 95% confidence interval.
Second, we calculated 14 network structure properties [32]
whose definitions and significance are discussed elsewhere
(table 1, Metrics 6–19 in [34]). The properties are the fractions
of top, intermediate and basal species (Top, Int and Bas); the frac-
tions of cannibals, herbivores, omnivores and species in loops
(Can, Herb, Omn and Loop); the standard deviations of normal-
ized total links, generality and vulnerability (LinkSD, GenSD
and VulSD); the mean short-weighted trophic level (SWTL); the
mean maximum species trophic similarity (MaxSim); the mean
shortest path length (Path) and the mean clustering coefficient
(Clus). We generated 1000 niche model webs [32] with thesame S and C as the empirical web, and for each property calcu-
lated model error (ME), the normalized difference between the
model’s median value and the empirical value [33]. ME. j1j
indicates that the empirical property falls outside the most
likely 95% of model values, with negative and positive MEs
indicating model underestimation and overestimation of the
empirical value, respectively. While these properties are not
independent [37], we are primarily concerned with systematic
patterns of change in average ME, as in prior studies [8,33,34].
Third, we used a probabilistic nichemodel (PNM) [39] to para-
metrize the niche model directly against each food web. The PNM
produces amaximum-likelihood estimate (MLE) of the fundamen-
tal niche model parameters for each species i in a given web: its
niche position ni, its optimal feeding position ci and its feeding
range ri. This allows computation of the probability of each link
in a web according to the model, and the overall expected fraction
of links in a web predicted correctly ( f L).
Model results for extant webs were taken from prior studies,
resulting in a set of 30 extant webs for MaxEnt and PNM ana-
lyses [38,39] and a subset of 11 extant webs for niche model
.012 0 39.0 61.0
.013 0 38.5 61.5
.046 0 43.3 56.7ber of trophic links; L/S, linkage density and C (L/S2), directed connectance.
ediate or high certainty. ‘Red.’ refers to reduced web versions that exclude
Cert-Low Cert-Int Cert-High
.013 22.4 31.9 45.7
.014 22.3 32.0 45.7
.059 27.6 30.8 41.6
.012 0 39.0 61.0
.013 0 38.5 61.5
.046 0 43.0 57.0
.013 22.4 31.9 45.7
.014 22.3 32.0 45.7analyses [33] (electronic supplementary material, table S1). We
also used the previously documented systematic decreases in
model fit with food web species richness or links per species
[33,34,38–40] as a further means of comparing webs of varying
diversity and complexity, an especially crucial issue for the
highly diverse Messel forest web.
3. Results
The full Messel food web consists of 700 trophically unique
taxa and 6444 links (electronic supplementary material,
figure S6) [41]. Fifty-four per cent of the taxa are resolved to
the genus or species level, and 82% to the family level or
better. The taxa consist of 187 plants (principally vascular
plants), 326 invertebrates (overwhelmingly insects), 143 ver-
tebrates and 44 protists, fungi and prokaryotes. Seventy-eight
per cent of the links have intermediate or high certainty
(table 1). The full Messel web was split into a Messel lake
web with 94 taxa and 517 links and a Messel forest web with
630 taxa and 5534 links, with 78% and 72% intermediate plus
high-certainty links, respectively (table 1 and figure 1). Only
one pair of taxa in each habitat web shares the same set of
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4predators and prey, resulting in trophic species versions of the
webs with 93 (lake) and 629 (forest) taxa. Reduced, higher
certainty versions of the Messel food webs that exclude low-
certainty links have 4–12% fewer taxa and 28–30% fewer
links (table 1). The two habitat-specificwebs have similarmaxi-
mum generality, as each contains a taxon that feeds on ca 30%
of taxa. However, theMessel forest web has a greater incidence
of trophic specialization, with 14%of taxa feeding on one taxon
(a)
(b)
Figure 1. Visualizations of the Messel lake and forest food webs. (a) Lake
food web and (b) forest food web. Spheres represent taxa, lines represent
feeding links. Links that loop indicate cannibalism. The vertical axis corre-
sponds to short-weighted trophic level [48], with autotrophic taxa and
detritus at the bottom level. Images produced with Network3D [49,50]. Col-
ours of nodes correspond to taxonomic affiliation of species. Green, plants,
including algae and diatoms; blue, bacteria, fungi and detritus; yellow, invert-
ebrates; orange, vertebrates.compared with 5% specialists in the Messel lake web.
Almost all aspects of the trophic structure of the Messel
lake web fit within the ranges observed for extant webs,
including its trophic species richness S of 93 and connectance
C (the proportion of possible links that are realized, L/S2) of
0.059 (table 1; electronic supplementary material, table S1).
The consumer distribution of the Messel lake web is margin-
ally significantly narrower than a null MaxEnt expectation
(electronic supplementary material, figure S7 and table S2),
but five of 30 extant webs have narrower distributions. The
resource distribution width is not significantly different
than the MaxEnt expectation, as is the case for 24 of 30
extant webs. The mean absolute niche ME for 14 metrics of
the Messel lake food web is exceeded by three of 11 extant
webs (electronic supplementary material, table S2), and the
number of individual metrics poorly fit by the niche model
in the Messel Lake web (six of 14) is equalled or exceeded by
three extant webs with 6, 8 and 12 poorly fit metrics (electronic
supplementary material, table S3). Considering particular
metrics, only the proportion of taxa that are basal (Bas) displays
an ME for the Messel lake web that falls outside the range of
ME across the extant webs (21.80, indicating model underesti-
mation), although two extant webs have similar ME of 21.50
(electronic supplementary material, table S3). The PNM cor-
rectly predicts 52.4% of Messel lake links, which is near the
low end but within the range for 30 extant webs (electronic
supplementary material, table S2).An assessment of where Messel lake web structure falls
compared to extant webs given linear scale-dependent trends
of model fit strengthen this assessment of similarities in net-
work structure. For extant webs, the absolute width of the
resource distribution (Res jW95j) (figure 2b) and the absolute
mean niche model error (jMEj) (figure 2c) significantly
increase with S (electronic supplementary material, table S4).
The fraction of links correctly predicted by the PNM ( fL)
(figure 2d) significantly decreases with S, and the width of
the consumer distribution (Con W95) (figure 2a) significantly
narrows with increasing L/S (electronic supplementary
material, table S4). The Messel lake web, with relatively high
S and intermediate L/S, fits within those trends (figure 2),
and its addition alters linear regressions based on extant
webs minimally (electronic supplementary material, table S4).
Comparing the Messel forest food web to extant webs is
more challenging than for the Messel lake web. With S of 629
and C of 0.014, the Messel forest web has far greater trophic
species richness than the largest extant web (S ¼ 155) and
lower connectance than the lowest extant web (C ¼ 0.034)
(table 1; electronic supplementary material, table S1). Its high
S and low C are likely attributable to very high resolution of
185 terrestrial plants, 323 mostly insect herbivores and their
trophic interactions, many of which are specialized. All
extant terrestrial web datasets and most aquatic datasets have
low resolution of plant taxa, invertebrate taxa and/or their
interactions. For example, a Caribbean reef web with 249
taxa, not included in this analysis owing to highly uneven res-
olution [3], has fish identified mostly to species comprising
84% of taxa, and invertebrates and primary producers highly
aggregated in groups comprising 14% and 2% of taxa, respect-
ively [3,51]. However, it is also possible that lower connectance
in the Messel forest web is in part an artefact of incomplete
detection of all fossil plant–insect trophic interactions.
Analysis of the structure of the Messel forest web reveals
a serious limitation of the niche model [32], which cannot
generate webs that are single connected networks for webs
with high S and low C. This limits possible Messel forest
web comparisons to link distributions and link probabilities.
The Messel forest consumer distribution is significantly nar-
rower than the MaxEnt expectation, and narrower than all
but one extant web (electronic supplementary material,
table S2 and figure S7). However, this level of narrowness
fits well with the significant trend of decreasing width of
Con W95 with increasing L/S (figure 2a; electronic supplemen-
tary material, table S4), given the Messel forest L/S of 8.79.
The absolute width of the resource distribution (Res jW95j)
of the Messel forest web is significantly wider than both the
MaxEnt expectation (electronic supplementary material,
figure S7) and extant web distributions (figure 2b), and the
PNM only predicts 26.6% of Messel forest links correctly
( fL), compared with the lowest value of 50.2% for an extant
web (figure 2d; electronic supplementary material, table S2).
As both the Res jW95j and fL display significantly decreased
model fit with increasing S (figure 2b,d; electronic sup-
plementary material, table S4), and the Messel forest has
high S, it is unsurprising that there are strong differences
compared with results for webs with S , 160. Indeed, the
position of the Messel forest’s Res jW95j and fL in relation to
S look like simple extensions of linear relationships observed
for webs with S, 160 (figure 2b,d), although significance
tests are not justified given the large gap between the
Messel forest data point and the other data points. Results
f L
Re
s |W
95
|
0
(b)
(d )
elative
distribu
d by th
bs, res
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1
2
3
6
4
2
0
–2
–4
0 5 10
Co
n 
W
95
m
ea
n
 |M
E|
links/species
no. species
15 20
0 50 100 150 20
(a)
(c)
Figure 2. Scale dependence of MaxEnt, niche model and PNM results. (a) R
density (L/S). (b) Absolute value of the relative width of the empirical resource
model error (jMEj) plotted against S. (d ) The fraction of links correctly predicte
Green and red triangles show results for the Messel forest and lake food wefor the higher certainty, reduced versions of the Messel lake
and forest webs are consistent with observed trends in struc-
ture across Messel and extant webs (figure 2; electronic
supplementary material, table S2), similar to earlier studies
which found that network structure patterns are robust to
removals of approximately 20–30% of links and associated
taxa [8,52]. It also is likely the case that both Messel and
extant food web data fail to include some links and species
that actually occurred. However, food web structure has
been shown to be robust to the addition of approximately
20% of species and links [52].
To better assess the impact of plant–insect interaction resol-
ution on Messel forest food web resource distribution width
(Res W95) and the fraction of links correctly predicted by the
PNM ( fL), we turned to highly resolved and well-sampled
species interaction data from Norwood Farm, UK [53]. While
not representing a full foodweb, a subset of the dataset includes
interactions between 95 plants and 312 herbivores which are
potentially comparable to interactions between the 185 plants
and 323 herbivores in the Messel forest web. In both cases,
the consumers are mostly insects. The trophic species version
of the Norwood bipartite herbivore–plant subweb has
Splant ¼ 91, Sconsumer¼ 146, L ¼ 939 and C ¼ 0.07, where C is
calculated as L/(Splant  Sconsumer), while the Messel subweb
has Splant ¼ 185, Sconsumer¼ 294, L ¼ 2127 and C ¼ 0.04. The
connectances of these two subwebs do not differ greatly,
suggesting that the low connectance of the full Messel forest
food web may reflect the attribute of high incidence of special-
ization between insect herbivores and plants more than the
artefact of low sampling of trophic interactions among a
highly resolved set of plants and insects.0.2
0.4
0.6
0.8
1.0
no. species
no. species
0 200 400 600 800
0 200 400 600 800
width of the empirical consumer distributions (Con W95) plotted against link
tions (Res jW95j) plotted against species richness (S). (c) Mean absolute niche
e PNM ( fL) plotted against S. Black circles show results for extant food webs.
pectively, with open triangles indicating results for reduced web versions.5
4
3
2
1Analysis of the linkdistributions indicates that both subwebs
have similar, and significantly broader resource distributions
than the MaxEnt expectation (Messel Res W95¼ 2.93, Norwood
Res W95 ¼ 3.11). This suggests that the apparent outlier status of
Res W95 of the full Messel Forest web is likely attributable to its
high resolution of plant–insect interactions. However, the
PNM correctly predicts 52% of Norwood links but only 26% of
Messel links. The Norwood data include about half as many
taxa and links as the Messel data, which suggests that much of
the difference in fL may be attributable to strong scale depen-
dence of PNM fit with S, observed for full food webs [39] as
well as for smaller herbivore–plant subsets of extant webs
[40]. In addition, the Norwood data, with a focus on aphids,
nectar/pollen feeders and seed consumers, lacks trophic
groups well-represented in the Messel data such as folivores
which may affect fL. Future compilation of comprehensive,
highly resolved food web data for modern systems, particularly
terrestrial systems with diverse insect–plant interactions,
will help fill in current data gaps and allow more definitive
comparisons of Messel forest and extant web structure.
4. Discussion
The Messel biota represents ecologically modern lake and
forest taxa occurring after a series ofmajor physical disruptions
and biotal reorganizations 18 Myr after major ecosystem
change at the K–Pg boundary [9–15] and subsequent signifi-
cant modification that continued throughout the Early
Eocene [16–26] (electronic supplementary material, table S5).
The evidence presented here suggests that the structure of
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6feeding interactions among Messel taxa was also modern
despite the major changes of the preceding 18 Myr and was
also apparently robust to the subsequent 48 Myr of species
turnover and evolution.
There is unambiguous evidence for the similarity of
Messel lake food web structure to that of extant webs. Com-
parisons of resource and consumer distributions, food web
metrics and the fraction of links correctly predicted by the
PNM place Messel lake web structure well within ranges
observed for extant webs. Those findings are strengthened
by evidence based on the scale dependence of model fit
with species richness S and link density L/S, which shows
that Messel lake food web results are consistent with
significant linear trends inmodel fit observed across extantwebs.
The evidence for the similarity of the Messel forest web is
suggestive but necessarily less definitive due to its much
greater species diversity and lower connectance than extant
webs and the Messel lake web, which allows for less direct
comparisons of detailed structure. Deviation of link distri-
butions from a MaxEnt expectations and the fraction of links
correctly predicted by the PNM indicate that Messel forest
web structure falls outside what is observed for extant webs
and the Messel lake web. However, the scale dependence of
the fit of those models indicate either that Messel forest struc-
ture fits well within observed scale-dependent trends in the
case of consumer distribution width (as a function of L/S) or
appears to be a result of decreased fit with increasing species
richness (i.e. absolute width of the resource distribution, frac-
tion of links predicted by the PNM). These results, as well as
a comparison of the herbivore–plant subnetworks of the
Messel forest and Norwood farm webs, suggest that apparent
differences in Messel forest web structure are likely attributable
primarily to its very high resolution and diversity compared to
other webs. This heightened characterization of the Messel
forest web results from a detailed accounting of plant–invert-
ebrate interactions thus far missing from extant food webs.
Future work to further elucidate similarities and differences
in Messel forest and extant terrestrial web trophic organization
could include comparisons of other kinds of plant–insect sub-
webs, for example, those that focus on herbivores and their
parasitoids and/or predators for a suite of plants or for a
particular plant [54–56].
Extant webs display fundamental similarities in trophic
organization across habitats [3,4], despite different kinds of
organisms filling similar ecological niches (e.g. large preda-
tory fishes versus mammalian carnivores). There are also
ecological differences in some trophic habits and niche-filling
in the Messel forest versus extant ecosystems. For example,
Messel Eomanis anteaters and Propalaeotherium horses have
very different diets than their modern descendants, and
large ground-dwelling carnivorous birds occupied ecological
niches filled today by top mammalian predators. But as with
extant webs, such substitutions are likely not associated with
fundamental changes in overall trophic organization.
Our analysis of the Messel forest web highlights limit-
ations in empirical and modelling aspects of current food
web structure analysis. The webs previously used to evaluate
network structure have species richness less than 160, and in
most cases have uneven resolution with highly aggregated
invertebrates and basal taxa and highly resolved vertebra-
tes. The Messel forest food web introduces new empirical
benchmarks for high diversity, high resolution of terrestrial
plant–insect interactions, and documentation of adjoining,interlinked habitats. Other highly and evenly resolved food
webs with S of 500–700 are needed for more direct compari-
sons of Messel forest and extant trophic organization and
to corroborate or reject our hypothesis of similar structure.
In addition, new data with S. 100 are needed to fill in
gaps in our understanding of the scale dependence of food
web structure and model fit. Regarding the simple models
used here, they appear to fit the structure of food webs with
S, 100 reasonably well, but that fit decays rapidly, systemati-
cally and linearly with increased S. Also, models like the niche
model [32] cannot be tested against very high diversity, low
connectance webs like the Messel forest owing to difficulties
in generating single connected component networks for com-
parison. Our analyses of the Messel forest web suggest that
more diverse and highly resolved data require development
and testing of new network structure models, and may require
a shift from low- to higher dimensional approaches.
The compilation of trophic information for other fossil
assemblages can provide opportunities to explore other aspects
of the stability of ecosystem organization over various geolo-
gic timescales [6–8]. For example, it has been suggested that
food web analysis can be used to look for changes in trophic
organization [8] and robustness [6,7,57] before, during and/
or after major extinction events. We have listed nine target
deposits comparable to Messel that span the 18 Myr interval
prior to Messel, and extend downward to the Late Cretaceous
(electronic supplementary material, table S5). Although food
webs of these freshwater and terrestrial ecosystems remain
unknown immediately preceding the K–Pg ecological crisis
and the Palaeogene prior to Messel, several major environ-
mental disruptions did occur, notably the PETM [16], several
EECO pulses [17] and the Azolla Event [25] (electronic sup-
plementary material, table S5). These major pulses involving
mostly palaeoclimatic change evidently had major conse-
quences in altering food web structure prior to Messel. A
food web analysis of a latest Cretaceous lake deposit ecologi-
cally analogous to Messel would reveal whether food webs
after the K–Pg crisis lacked significant trophic reorganization
[58,59], or underwent rapid and possibly permanent change
associated with a prolonged recovery [11–13]. The latter
would have entailed a several million-year interval of signi-
ficant habitat and community reorganization, fostering
regional trophic cascades that may have resulted in changes
in food web properties such as connectance, trophic level,
path length and link distributions, which reflect the balance
of specialization and generality of feeding habits, and the bal-
ance of vulnerability and invulnerability to predation.
Successive analyses of trophic structure over deep time
(electronic supplementary material, table S5) could potentially
be used to assess other interesting questions. We provide
two examples. First, are there similarities between ecological
assemblies of food webs at very short timescales following
localized perturbations versus evolutionary assembly of food
webs at very long timescales following major extinction
crises? A recent study of the dynamics of food web structure
on defaunated mangrove islets showed an increase in pro-
portion of species that are specialists and a decrease in
connectance over 2 years’ reassembly time [60]. It may be the
case that evolutionary assembly of food webs over geologic
time following an extinction crisis would also tend to favour
generalists at early stages and specialists at later stages, altering
link distributions and connectance as well as other properties.
In addition, researchers have begun to explore models of
food web development based on simple evolutionary and
to
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12 917–12 922. (doi:10.1073/pnas.192407699) 11. Wing SL, Herrera F, Jaramillo CA, Go´mez-Navarro C,
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eotropica
27–18 6
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arcot J,
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folivory tracks paleotemperature for six million years.
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